ICES BEWG Report 2007
ICES Marine Habitat Committee
CM 2007/MHC:10
REF. ACE
Report of the
Benthos Ecology Working Group
(BEWG)
23-27 April 2007
Wilhelmshaven, Germany
International Council for the Exploration of the Sea
Conseil International pour l’Exploration de la Mer
H. C. Andersens Boulevard 44–46
DK-1553 Copenhagen V
Denmark
Telephone (+45) 33 38 67 00
Telefax (+45) 33 93 42 15
www.ices.dk
info@ices.dk
Recommended format for purposes of citation:
ICES. 2007. Report of the Benthos Ecology Working Group (BEWG), 23–27 April 2007. CM
2007/MHC:10. 99 pp.
For permission to reproduce material from this publication, please apply to the General
Secretary.
The document is a report of an Expert Group under the auspices of the International Council
for the Exploration of the Sea and does not necessarily represent the views of the Council.
© 2007 International Council for the Exploration of the Sea
ICES BEWG Report 2007
Contents
Executive summary.......................................................................................................... 1
1
Opening of the meeting ........................................................................................... 3
1.1
Appointment of Rapporteur............................................................................. 3
1.2
Terms of Reference ......................................................................................... 3
2
Adoption of the agenda ........................................................................................... 3
3
Report on ICES meetings and other meetings of interest .................................... 3
3.1
ASC 2006 (Maastricht) / ICES Annual Report for 2006 ................................. 3
3.2
Marine Habitat Committee, Maastricht 2006 .................................................. 3
3.3
WGEXT........................................................................................................... 3
3.4
MarBEF ........................................................................................................... 4
3.5
WGECO .......................................................................................................... 4
3.6
Other meetings................................................................................................. 4
3.6.1 WKNEPHTV...................................................................................... 4
3.6.2 Workshop on taxonomy of macrophytes ............................................ 5
3.6.3 ASC 2007 ........................................................................................... 5
4
Assess and report on changes in the distribution, population abundance
and condition of benthic invertebrates in the OSPAR maritime area in
relation to changes in hydrodynamics and sea temperature (ToR a).................. 5
5
Assess and report on the extent to which the changes reported in (a) can
reliably be attributed to changes in hydrodynamics and sea temperature
(further details on the interpretation and handling of this ToR will be
provided by ACE) (ToR b)...................................................................................... 5
6
Assess and report on the evidence on which the nomination of Seagrass
Cymodocea meadows for the OSPAR List of Threatened and/or Declining
Species and Habitats is based (ToR c) ................................................................... 6
7
Discuss and report on quality assurance and control guidelines for
sampling and analytical practices for benthos (ToR d)........................................ 7
8
Review and consider recent developments in ongoing benthos research in
the ICES area (ToR e) ............................................................................................. 7
8.1
Cooperative studies.......................................................................................... 7
8.1.1 MAFCONS......................................................................................... 7
8.2
Benthos and fisheries....................................................................................... 7
8.2.1 BWZee................................................................................................ 7
8.2.2 HABMAP ........................................................................................... 8
8.3
Benthos of soft sediments................................................................................ 9
8.3.1 Long-term benthos studies in German waters..................................... 9
8.3.2 Long-term benthos study in the Netherlands .................................... 10
8.4
Benthos of rocky substrates ........................................................................... 10
8.4.1 Phytobenthos in the Baltic ................................................................ 10
8.5
Other studies.................................................................................................. 11
8.5.1 Biological criteria review for the selection of dredged material
disposal sites: European examples of best practices at sea. .............. 11
8.5.2 SPEEK .............................................................................................. 11
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8.5.3
8.5.4
8.5.5
8.5.6
MACROBEL .................................................................................... 11
Prestige Oil Spill .............................................................................. 11
Gulf of Gdansk benthic habitat spatial mapping............................... 12
Studies in Portugal............................................................................ 12
9
Assess the effectiveness of any potential performance indicators in
identifying cause-effect relationships based on a list of indicators prepared
by intersessional work (ToR f).............................................................................. 12
10
Discuss and report on the role of benthos for monitoring under the WFD
and the NATURA 2000 regimes (ToR g) ............................................................. 13
11
Based on the final SGNSBP report discuss further plans for North Sea
benthic surveys (ToR h) ........................................................................................ 14
12
Discuss recent developments in benthic sampling methodology with a view
on updating the TIMES No. 27 recommendations (1999) (ToR i)..................... 15
12.1 TIMES no. 27 recommendations................................................................... 15
12.2 Sieving alive or after fixation ........................................................................ 15
12.3 Van Veen grab - Hamon grab comparison .................................................... 15
13
Report on the environmental implications of existing off-shore renewable
energy generation installations (wind, wave, tide, etc.) and make proposals
to minimize their negative effects (ToR j)............................................................ 16
14
Any other business................................................................................................. 16
14.1 Upcoming Symposia...................................................................................... 16
14.1.1 42nd European Marine Biology Symposium (EMBS)....................... 16
14.1.2 Conference of the Estuarine Research Federation 2007 (ERF
2007)................................................................................................. 16
14.1.3 10th International Conference on Shellfish Restoration (ICSR)........ 16
14.1.4 ICES Symposium on Environmental Indicators: Utility in
Meeting Regulatory Needs ............................................................... 16
14.2 Workshop/symposia proposals ...................................................................... 16
14.3 BEWG website .............................................................................................. 16
14.4 LYYN T38 Real time image enhancer .......................................................... 17
14.5 Taxonomic help ............................................................................................. 17
15
Adoption of report ................................................................................................. 17
16
Closing of the meeting ........................................................................................... 17
Annex 1: List of participants ....................................................................................... 18
Annex 2: BEWG Agenda ............................................................................................. 20
Annex 3: BEWG Terms of Reference 2006 ................................................................ 22
Annex 4: Draft resolutions for next year .................................................................... 24
Annex 5: Benthos and climate change in the Bay of Biscay...................................... 28
Annex 6: Red Lists in Germany .................................................................................. 29
Annex 7: Report on benthos changes in the OSPAR area ........................................ 30
Annex 8: Long-term series in The Netherlands ......................................................... 40
Annex 9: Current activities of the benthos group of IPIMAR.................................. 45
ICES BEWG Report 2007
Annex 10: Long term changes in the phytobenthic communities of the Baltic
Sea ........................................................................................................................... 56
Annex 11: Final report on the effects of the Prestige oil spill on continental
shelf macroinfauna (Galicia, NW Spain) ............................................................. 58
Annex 12: Spatial and temporal changes in benthic communities of the
Galician continental shelf after the Prestige oil spill .......................................... 76
Annex 13: Monitoring the Prestige oil spill impacts on some key species of the
Northern Iberian shelf........................................................................................... 77
Annex 14: List of metrics (updated from SGSOBS 2004)......................................... 78
Annex 15: Different impact sources and geographical areas for which AMBI
has been applied, in recent years.......................................................................... 83
Annex 16: Benthos ecological status assessment and monitoring for the Water
Framework Directive in the Belgian coastal waters ........................................... 86
Annex 17: Methods used in Europe, for the Water Framework Directive By
Angel Borja (AZTI-Tecnalia, Spain) ................................................................... 89
Annex 18: Atlantic intercalibration ............................................................................ 90
Annex 19: Sieving comparison .................................................................................... 92
Annex 20: NSBP CRR.................................................................................................. 93
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ICES BEWG Report 2007
Executive summary
Highlights
•
A subgroup of the BEWG (SGNSBP) finished a comprehensive report (CRR) on
the North Sea Benthos Project 2000 in which they deliver a valuable dataset on
the benthos of the North Sea together with long-term evaluations and model
developments.
•
Reports from current benthos work in Europe revealed positive news that the
PRESTIGE oil disaster in NW Spain had no lasting negative effects on the
benthos, and the Baltic coastal region in east Sweden shows signs of general
ecological improvement as seen by a deepened distribution of algae and
decreased nitrate concentrations in the water.
The BEWG held its 2007 meeting at the Senckenberg Institute, Wilhelmshaven, Germany. 18
participants from seven countries attended and concentrated on the challenging agenda and
also reported on benthos research on-going in Europe.
ToR a and b: The question concerning the effects of changing hydrodynamics and sea
temperature on benthic communities cannot be answered without difficulties. Observations on
a smaller scale may give contradicting results. On a large scale, changes in hydrodynamics
and sea temperature are often interconnected and are a result of climatic variability as
indicated by the NAO index.
With regard to changes of hydrodynamics there is only little information available. On the
Dogger Bank increased current velocities caused changes in sediment composition and as a
consequence also in the benthic community. Off the English east coast hydrographic changes
were considered responsible for changes in food availability (derived from phytoplankton) to
the benthic community.
Changes in the characteristics of winters and summers play an important role in structuring the
benthos.
If the trend of milder winters and warmer summers, also expressed by the NAO index,
continues, shifts in species composition and numbers, abundance and biomass can be
expected, as it is being recorded now for some of them.
No species can be named as being specifically responsible for changes in hydrodynamic
conditions, whereas a temperature increase is indicated by shifts in the distribution of a range
of several species, e.g., Megaluropus agilis and Amphiura brachiata in OSPAR region II, e.g.,
in OSPAR region IV and species region II.
ToR c: The Chair answered an intersessional OSPAR request concerning listing of
Cymodocea meadows in southern Europe. They were consequently listed as endangered.
ToR e: Highlights of the reports were the documentation of the improvements of the coastal
ecosystem at the eastern Swedish coast as evidenced by deeper algae distribution compared
with historical pre-industrial records and decreasing nitrate concentration in the water. The
phosphate levels seemed nevertheless to increase. This could be a result of increased
bioturbation in the sediment due to the improved environmental conditions.
A national project in Belgium on Marine Biological Valuation revealed exciting new ways to
value ecologically important sites in a non-monetary fashion. It will shortly be combined with
MarBEF attempts to enlighten the socio-economic sides of biodiversity research.
The final report on the Prestige oil disaster in NW Spain showed in the end no lasting effects
in the benthic system although the argumentation was hard since there were no pre-event
monitoring data except some epifauna records. Tar clumps in the deeper waters are no longer
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ICES BEWG Report 2007
visible as there are no visible effects in the coastal ecosystem. Also the coastal fishery is back
to normal and the lesson learned is that recovery is a normal process in nature.
ToR d and i: New improved methodical investigations were reported as method
harmonization and standardisation was always one of the prime aims of the group. This was
the sieving of fresh material vs. fixed material and a comparison of the widely used Van Veen
grab and the Hamon grab which is mainly used in coarse sediments. The TIMES 27 document
was revised and an updated version is almost ready for publication.
ToR f: The group updated the list of metrics and recommended the organisation of a
workshop on benthos related environmental metrics.
ToR h: The SGNSBP presented its final reports in the form of and CRR draft just submitted
to ICES for publication. Most of the material presented here was also used to answer the
OSPAR requests under ToR a and b. The group is planning a new North Sea benthos project
in 2010.
ICES BEWG Report 2007
1
Opening of the meeting
The Chair, Heye Rumohr, opened the meeting and welcomed the participants. The local host,
Ingrid Kröncke from the Senckenberg Institute gave some practical information about
domestic issues. A list of participants is included at Annex 1.
An ICES sharepoint site was made available during the meeting and proved to be a valuable
tool to speed up the work and make exchange of information more efficient. The Chair
emphasized the importance of taking OSPAR request very seriously as they are important for
ICES advisory work.
Apologies were received from J. Craeymeersch, Silvana Birchenough, Hubert Rees, Kerstin
Mo, Lene Buhl-Mortensen, B. Tunberg, Jan van Dalfsen and A. Schroeder.
1.1 Appointment of Rapporteur
The Chair expressed his wish to have daily Rapporteurs, together with an editing Rapporteur
who would bring the daily contributions together into the final report. H. Hillewaert was
appointed editorial Rapporteur; daily Rapporteurs were I. de Boois, I. Moulaert, M.
Robertson.
1.2 Terms of Reference
The Terms of Reference (ToR) for BEWG 2007 are listed at Annex 3. The respective ToR
item is included in the headings of subsequent sections for information.
2
Adoption of the agenda
The agenda was agreed unanimously and is attached at Annex 2.
3
Report on ICES meetings and other meetings of interest
3.1 ASC 2006 (Maastricht) / ICES Annual Report for 2006
H. Rumohr reported briefly on the ASC 2006. Mainly fish and management subjects were on
the agenda and only a few environmental topics. To improve this uneven situation we need
more activities and input from the environmental side of the ICES community. The report is
on the ICES website and can be downloaded from there.
3.2 Marine Habitat Committee, Maastricht 2006
H. Rumohr reported, as outgoing MHC Chair, on the creation of a new study group within the
Marine Habitat Committee: namely the SGBIODIV (the Study Group on Biodiversity
Science), this group will continue to review all MarBEF-work undertaken within ICES. Dr
Hubert Rees will be the first Chair of this group.
The Marine Habitat Committee has a new Chair, Tom Noji (NOAA) from the USA.
3.3 WGEXT
H. Hillewaert, reported on the recent WGEXT meeting in Helsinki, Finland. A summary by
Kris Hostens (ILVO, Belgium) is given below.
For each member country, the total extracted amount of sand and gravel in 2006 was reported
and the development of EIA's and marine resource and habitat mapping programs were
reviewed. Much time was spent on finalizing the Cooperative Research Report, which wasn't
finished during the last year due to a variety of circumstances. However most of the chapters
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are now ready. Only the executive summary and the final editing of the Report need to be
completed. The final report will be sent for publication by May/June 2007. The group also
started to review the ICES Guidelines on sand extraction monitoring and the
complementarities/overlap of the COST-Maggnet action with the work of the ICES WGEXT
group were discussed.
An interesting (and to several of the participants astonishing) presentation was given by Ad
Stolk (Netherlands) about the 'Extraction of sand for the enlargement of the Rotterdam
harbour'. The EIA describes the effects of large scale marine sand extraction with a maximum
of 365 million m³ (see www.maasvlakte2.com for the Environmental Impact Assessment).
Jan Van Dalfsen gave a short overview of the MESH project (Mapping European Seabed
Habitats - http://www.searchmesh.net), where much effort has gone into the development of
state-of-the-art digital databases of various bathymetric, sedimentological and biological
parameters. These digital databases can be queried and analyzed rapidly, will enable
intercomparison to establish relationships, and make it possible to produce tailor-made maps
on demand. Another presentation was given by Michel Deprez on 'the trophic role of benthic
communities for the main commercial demersal fish species in Dieppe'. (Actually this is one of
the recommendations of this group which still little attention). Results were also presented
from the monitoring program of the construction works underway in the new Port of Helsinki
in 2005.
(http://www.vuosaarensatama.fi/linked/fi/tiedotteet/vesisto_2006.pdf).
WGEXT is planning to take a clear look at the use of the guidelines for sand and gravel
extraction. However, this will be dependent on the area studied, country, etc. For this review,
WGEXT requested that BEWG consider how to create a list of standard areas.
The WGEXT will next meet in the UK from the 8–11 April 2008.
3.4 MarBEF
H. Rumohr reported on MarBEF (a network of excellence for biodiversity research in
Europe). A special RMP project on recovering historical data, lead by staff from VLIZ
(http://www.vliz.be) is currently working. The next General Assembly will be held in Poland
during May 2007.
3.5 WGECO
I. de Boois briefly reported on benthos issues under WGECO. BEWG will assess benthos
information in the recent WGECO report. It is not clear whether WGECO expected BEWG to
create input for their meeting. The BEWG Chair will contact the WGECO Chair for
clarification.
3.6 Other meetings
3.6.1
WKNEPHTV
H. Rumohr reported on the newly formed WKNEPHTV (Workshop on the use of Under
Water TV surveys for determining abundance in Nephrops stocks throughout European
waters). This group aims to assess Nephrops by employing imaging as an
addition/complement to traditional fishing surveys. It was a useful meeting where fishing and
benthos interests met. The aim was to use non-destructive methods for stock assessments of
Nephrops. However not only Nephrops were counted on the images, other benthic organisms,
for example sea pens, was also observed. A CRR (Co-operative Research Report) is a likely
outcome out from this meeting.
ICES BEWG Report 2007
3.6.2
Workshop on taxonomy of macrophytes
H. Rumohr mentioned a workshop on the taxonomy of Baltic macrophytes. The resulting
report contains a useful identification tool.
3.6.3
ASC 2007
ASC 2007 will be held in Helsinki, Finland. There will be a Theme Session (A) chaired by
members of the BEWG on benthic dynamics in ICES waters. Presentations in this Theme
Session will focus mainly on the NSBP 2000 but other projects are welcome. Abstracts should
be submitted before the end of April 2007.
4
Assess and report on changes in the distribution, population
abundance and condition of benthic invertebrates in the
OSPAR maritime area in relation to changes in hydrodynamics
and sea temperature (ToR a)
K. Essink introduced a document prepared by a subgroup of the Working Group on aspects of
changes in benthic communities from within the OSPAR area. The paper described temporal
trends over the period between 1986 and 2000 and presented a compilation of long-term
studies in the OSPAR region.
A. Borja presented a talk entitled “Benthos and Climate Change in the Bay of Biscay”. An
outline of his talk is in Annex 5.
The data presented were extremely useful and will be added to the compilation paper
described by K. Essink previously. It was pointed out that there was a strong correlation
between changes noted in the fauna and the North Atlantic Oscillation (NAO) and with light
and suspended solids levels in the water column. For example, Gelidium biomass was closely
correlated with light levels. Secchi disc depth data were unfortunately not available.
E. Rachor reported on the ongoing work in Germany revising the Red List of endangered and
potentially endangered species of marine benthic invertebrates.
This will be the 3rd revision of these marine species lists (1984, 1998, 2008) and the aim is to
revise all German Red Lists every ten. The assignment of species to the Red List is controlled
by four main criteria: status of the population, long-term trend, short-term trend, additional
(new) risk factors.
From more than 2000 species, 600 were studied in detail and it is expected that up to 200 will
be placed in the final list. (Tables in Annex 6).
5
Assess and report on the extent to which the changes reported
in (a) can reliably be attributed to changes in hydrodynamics
and sea temperature (further details on the interpretation
and handling of this ToR will be provided by ACE) (ToR b)
A subgroup regarded Tor a and b together and formulated a combined report on both TORs.
See Annex 7.
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6
Assess and report on the evidence on which the nomination of
Seagrass Cymodocea meadows for the OSPAR List of
Threatened and/or Declining Species and Habitats is based
(ToR c)
This ToR item was intersessionally covered by the Chair after consultation with an external
panel of experts.
The Chair posed the OSPAR request to the members of the BEWG and had only few
substantial answers because the subject was beyond the expertise of the group as Cymodocea
grows only in southern Spain and on the Canary Islands. Nevertheless answers were received
from two senior members of the Working Group who argued that Cymodocea meadows
should be treated in a similar manner to endangered Zostera and Posidonia stands since they
suffer similar threats. The Chair also contacted colleagues who work on Cymodocea meadows
in Cadiz Bay and on the Canary Islands namely:
•
In Andalusia: Ignacio Hernández (ignacio.hernandez@uca.es) and Juan José
Vergara (juanjose.vergara@uca), both from the University of Cádiz;
•
On the Canary Islands: Inmaculada Santana Ojeda (macu@iccm.rcanaria.es),
from the Canary Institute of Marine Sciences;
and received useful answers from Ignacio HERNANDEZ: “We are presently studying the
meadows of Cymodocea in the Cadiz Bay. In 2007 two theses will be finished about the
biomass and growth dynamics of Cymodocea nodosa. The next step will address the
interaction of these meadows with Caulerpa prolifera. This chlorophyte is spreading into
Cymodocea meadows but at present we cannot assess whether Cymodocea is declining or not
in Cadiz Bay. It may be possible but we need to address the question of the patch distribution
of Caulerpa first. This species grows under very different sediment conditions than those of
Caulerpa, but at the moment we do not know if the sediment is cause or consequence of the
covering by Caulerpa. In Cadiz Bay, Cymodocea meadows are suffering from different
impact, including eutrophication, dredging and water turbidity by shell-fishing. In case you
need further information about biomass dynamics of Cymodocea (although still unpublished)
please let me know. We have been looking carefully at the document and consider that the
data are reliable. The following comments may improve the sheets about Cymodocea.
Comments to OSPAR list::
•
Definition for habitat mapping. Cymodocea nodosa forms large and dense
patches with green leaves that can reach up to 100 cm long and 8.0 mm wide.
•
Geographical extent. Seeds have been recorded in Cadiz Bay but probably many
seedlings are not successful. In Cadiz Bay there are intertidal meadows of
Cymodocea which are exposed for several hours during a tidal cycle
•
Decline. Probability of significant decline in Cadiz bay YES. The main impact is
construction works (harbours, factories, roads...) that cause water pollution within
the habitat.”
The Chair’s personal view and answer to ACE was “Cymodocea meadows are, at least in
Cadiz Bay, candidates for nominations for the OSPAR List of Threatened and Declining
Species as set out in the table presented by OSPAR. The data used to support the nominations
are sufficiently reliable and adequate to serve as a basis for conclusions that the species and
habitats concerned can be identified as threatened and/or declining species and habitats
according to the Texel/Faial criteria. There were no indications from experts that the presented
evidence was not sufficient or unreliable. But special attention should be paid to the
interaction/ competition with Caulerpa prolifera. The coming thesis/report by Hernandez and
Vergara (University of Cadiz) should be used as baseline information once it is available. The
proposed amendments for the OSPAR list should be checked for inclusion”.
ICES BEWG Report 2007
But, since there was no information about the present situation on the Canary Islands this
could only be adopted under precautionary aspects for the Canary Island region.
This intersessional answer was well received by the ACE Chair and the advice to OSPAR was
to include it in the relevant list as endangered what was finally also agreed on.
7
Discuss and report on quality assurance and control
guidelines for sampling and analytical practices for benthos
(ToR d)
The group discussed new QA matters concerning benthos sampling and sample processing
and used the results in the update of the TIMES 27 document under ToR i)
8
Review and consider recent developments in ongoing benthos
research in the ICES area (ToR e)
8.1 Cooperative studies
8.1.1
MAFCONS
H. Reiss reported on the EU-project MAFCONS (Managing fisheries to conserve groundfish
and benthic invertebrate species diversity). This project started in 2003 and was finalised in
autumn 2006. The main objective was to provide scientific advice to fisheries managers with
mathematical tools to quantify the consequences of fishing on demersal fish and benthic
invertebrate species diversity (for details see BEWG-Report 2005). The Houston’s dynamic
equilibrium model was used as a starting point to describe the relationships between
disturbance due to fishing activities and diversity. This model predicts that both positive and
negative responses of diversity to increased disturbance are possible, depending upon local
productivity.
The main spatial scale on which the studies of MAFCONS are based, was the ICES statistical
rectangle scale in the North Sea. Thus infauna (van Veen grab), epifauna (2 m beam trawl)
and fish (GOV) were sampled over the entire North Sea in summer 2003 and 2004. Secondary
production and diversity for each component have been determined and compared. The final
testing of Houston’s model showed that it could not provide a basis for predicting the
relationship between diversity and disturbance at least on the spatial scale studied. Therefore,
the development of an alternative size-structured species-interactive model was initiated.
All final reports can be downloaded from the project web-site (http://www.mafcons.org). The
infauna, epifauna and demersal fish datasets as well as a compilation of international annual
fishing effort and landings will be available after publication of the main parts of the project.
The group highlighted the importance of the availability of the data. Final storage location of
the data after the end of the project is still undecided.
8.2 Benthos and fisheries
8.2.1
BWZee
S. Degraer gave an overview of the project BWZee (A Biological Valuation Map for the
Belgian Continental Shelf.).
Decision support systems (DSS) for sustainable marine management should take account of
social and economic as well as ecological aspects. The project on marine biological valuation
aims at establishing a protocol to provide an integrated view on nature’s intrinsic value.
Biological value is defined here as the value of biodiversity, without any reference to
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anthropogenic use. As such, the biological value complements the social and economic
valuation within a DSS.
Till now, when requested, the biological value of an area was assessed through a basically
unguided procedure, primarily based upon a - best available expert judgement. Such
subjective and arbitrary procedures largely contribute to the general ignorance of biological
value within current DSSs. Our marine biological valuation protocol, in contrast, should
ideally be (1) scientifically widely acceptable, to avoid an uncontrolled proliferation of
valuation strategies, and (2) widely applicable, to maximise its applicability. Only when both
criteria are fulfilled, will the valuation protocol be taken into DSSs to quantify nature’s
intrinsic value. The successful application of such a protocol was taken from the terrestrial
part of Flanders (Belgium).
A review of relevant literature was first completed. From this, lessons were learned,
specifically: (1) the high redundancy in valuation criteria used, (2) the high variability in
valuation criteria and (3) the frequent confusion between valuation criteria and criteria for
MPA selection. A draft paper, drawn from this literature review, was taken as a starting point
for an international expert workshop on marine biological valuation. As a result of the
workshop a proposition for three first order valuation criteria and two modifying criteria were
fixed into a concept for biological valuation, taking into account all levels of biodiversity
organization (from genes to ecosystems). This concept for biological valuation strategy has
recently been published: Derous et al., 2007, Oceanologia.
The developed marine biological valuation protocol was then tested in the Belgian part of the
North Sea (BPNS). For all valuation criteria and organizational levels of biodiversity
assessment questions were described, leading to a protocol for biological valuation. These
were evaluated for the different ecosystem components for which data were sufficiently
available for the BPNS (seabirds, macro-, epibenthos and demersal fish). This leads to
different maps for every assessment question per ecosystem component. In a last phase of the
test all separate maps need to be combined and this will result in a marine biological valuation
map for the BPNS.
Within the NoE MarBEF Theme III Responsive Mode Action on DSSs and the CA ENCORA
Theme 7 on Biodiversity Change the protocol is now being tested or will be tested at eight
other sites, spread throughout European marine waters: Pico-Faïal channel (Portugal); Puscz
Bay (Poland), Scilly Islands (U.K.), Flamborough Head (U.K.), Northern French coastal area
(France), Adriatic Sea (Italy) and Sylt-Rømø (Denmark). These tests should provide us with
“lessons learned”, considering the general applicability of the protocol and it’s scientific
acceptability (i.e. feed back with local experts) and will thus lead to suggestions for further
improvement. The next workshop on these test cases is planned for Paris in November 2007.
Unlike the Bird and Habitat Directive, BWZee only takes the biological value into account,
not the degree of threat, political concern, vulnerability, socio-economic criteria, etc.
Project website can be found at http://www.vliz.be/projects/bwzee/.The final report on this
Belgian project will be available from the Belgian Science Policy website.
(http://www.belspo.be/belspo/home/publ_en.stm).
8.2.2
HABMAP
M. Robertson (FRS, Aberdeen) described progress with the two year HABMAP project. This
work builds directly on the fieldwork undertaken and results obtained during the EC funded
MAFCONS project. Samples and information gathered during MAFCONS will provide
benthic and fish community data from sites surveyed acoustically thus allowing investigations
into the link between habitat heterogeneity and species diversity. Identification of structural
ICES BEWG Report 2007
features that provide essential habitat for a variety of vertebrate and invertebrate species is
essential to furthering the ecosystem approach to fisheries management.
HABMAP started in April 2006 and all data gathering was completed by March 2007. Over
this time, three cruises were completed (one in the North Sea in August 2006 and two off the
Scottish west coast in November 2006 and March 2007 respectively). During each cruise,
acoustic data were logged from a series of intensively surveyed 3NM by 3NM boxes which
were drawn up around the immediate area surrounding and including the track of a trawl haul
undertaken for the International Bottom Trawl Survey (IBTS). Further to this, data were also
gathered from the survey vessel’s cruise track when approaching and leaving each trawl
position. These data will determine how representative the habitat type and variability
observed in the small boxes and the vessel track are of the larger ICES rectangles in which
they are contained and will also allow assessment of the extent to which the single trawl
samples in particular ICES rectangles provide representative samples of the fish assemblage
occupying each rectangle.
Although no formal habitat maps have yet been produced, acoustic data, ground truthing and
infaunal grab samples have been collected from 20 ICES rectangles in the North Sea and from
12 ICES rectangles on the west coast of Scotland.
During the second, final year of HABMAP, it is planned to complete all cleaning and database
preparation for the data collected from the intensive survey boxes and from the IBTS tracks
during the three cruises completed in 2006 and 2007. Also to report the results of all analyses
undertaken and to interpret habitat types and habitat distributions in relation to the biological
data collected in MAFCONS
Some other acoustic systems, such as side scan sonar at 410-450 kHz, have the resolving
potential for biota imaging. Patches of individual Lanice reefs can be discriminated with this
technique.
Synthetic Aperture Radar (SAR) has been looking promising for some years, but no members
of the group so far use this method.
Fast still image systems (2 fps) are being pioneered by US colleagues.
(http://habcam.whoi.edu/)
A special issue of the publication Remote Sensing of Environment on remote sensing of the
marine environment is due to be published later this year.
(http://www.elsevier.com/wps/find/journaldescription.cws_home/505733/description#descript
ion).
8.3 Benthos of soft sediments
8.3.1
Long-term benthos studies in German waters
I. Kröncke gave an overview on long-term benthos studies in German waters.
•
Infauna from Norderney has been collected since 1978. From 1978–1992 stations
were sampled monthly however, from 1992 onwards, they were only sampled
three times a year. Sampling up to 1995 has been reported; at this moment
analysis is done on the data from 1995 onwards. Especially interesting is the
development of the benthos after the very cold winter in 1995.
•
Infauna has been sampled along a transect running from the inner German Bight
→ Dogger Bank since 1990. The biological effects of contamination have been
sampled each May since 1995. All samples collected from 1995 until 2003 have
been analysed. A paper by Reiss about a comparison of the inshore-offshore has
also been published
|9
10 |
ICES BEWG Report 2007
•
Infauna Doggerbank. Decadal scale: 1950s, 1980s, 1990s, 2006/2007. Shows an
increase of southern species and a decrease in northern species.
•
Epifauna communities from the Greater German Bight have been investigated
every July/August from 1998 onwards. Sampling followed the IBTS format
where one haul was collected in each rectangle with a 2 meter beamtrawl.
•
Epifauna communities in 6 boxes running from the German Bight towards the
Norwegian Sea have been investigated since 1998. This sampling attempts to get
an overview about differences brought about by climate change in different areas.
Sampling is carried out once a year.
•
Epifauna from the Jade area has been collected since 1972. The dataset is hardly
analysed, but this might be done in a new project.
The Netherlands and Germany agreed on combining 2 meter beamtrawl data since 1998
(Germany) and 1999 (Netherlands) for analysis. German sampling is in the German Bight; the
Dutch sampling is mainly in the Southern and Central North Sea.
8.3.2
Long-term benthos study in the Netherlands
I. de Boois presented a long-term benthos study in the Netherlands (by J. Craeymeersch IMARES). In the Dutch coastal area dredge sampling has been carried out since 1995. It was
originally known as the Spisula-survey but since 2006 it has been renamed the Ensis-survey.
Spisula subtruncata stock has decreased very much in the survey period while Ensis sp. has
increased. The complete document is attached in Annex 8.
8.4 Benthos of rocky substrates
8.4.1
Phytobenthos in the Baltic
H. Kautsky reported on phytobenthos research in the Baltic.
Fucus vesiculosus sampling was first carried out in 1942 (‘pre-industrial data’) and then in
1984, 1992 and 2006. Between 1942 and 1984 the depth at which Fucus vesiculosus was
recorded decreased. In 1992 Fucus vesiculosus showed a slight increase in coverage while in
2006 the species reappeared at the same depths as first recorded in 1942. The trend is even
more visible when looking at one station at a time. Disappearance of species might be caused
by different processes such as competition, pollution, climate change, etc. However, the main
reason that Fucus vesiculosus plants disappear is because they reach the end of their lives. The
F. vesiculosus life cycle is quite complicated and unpredictable, so the species might
disappear for some time and then suddenly reappear. This not only is the case with Fucus
vesiculosus, but also happens in other species, e.g. Zostera communities.
Some factors that determine the depth distribution of phytobenthos are: substrate, light,
population dynamics, salinity.
If the increase in depth distribution of Fucus vesiculosus is due to increased water quality,
then this has to be measurable in e.g. Secchi depth data. However, this is not the case at all
sampling sites where nutrients often exhibit a slow decrease. For example, in the sampling
sites in the Baltic Sea, all nutrient fractions except phosphorus did decrease. Spring bloom
levels of chlorophyll-a are also decreased. This leads to the conclusion that the Baltic Sea
coastal ecosystem is recovering.
H. Kautsky also talked on survey methods and results used when surveying and describing
phytobenthos in Swedish waters as part of SCOPE (EU_WFD work).
ICES BEWG Report 2007
| 11
8.5 Other studies
8.5.1 Biological criteria review for the selection of dredged material
disposal sites: European examples of best practices at sea.
The draft version of this paper was reviewed during the meeting. The group agreed that the
main adjustments to be made to the document are: to include more references, to improve the
structure and to focus more on the made on the biological criteria. The group will send these
comments back to the main author of the paper (who could not attend the meeting) and
attempt to work by correspondence to finalise the paper for publication as soon as possible.
8.5.2
SPEEK
I. Moulaert informed the group on the status of the SPEEK (Study of post-extraction
ecological effects in the Kwintebank sand dredging area) report.
(http://www.belspo.be/belspo/home/publ/pub_ostc/EV/rappEV38_en.pdf).
8.5.3
MACROBEL
The Macrobenthos Atlas of the Belgian part of the North Sea was published in 2006. A free
copy can be ordered from:
http://www.belspo.be/belspo/fedra/proj.asp?l=en&COD=MN/DD2/013#docum
8.5.4
Prestige Oil Spill
S. Parra reported on the Prestige oil spill study.
After the grounding of the tanker Prestige on November 2002 near the Galician Bank, NW
Spain, about 50000 tons of heavy oil (type M-100) was released to the sea, affecting a huge
part of the Galician coastline and surroundings areas. Documents presented in 2003, 2004 and
2005 to this working group dealt with the general information about this oil spill, as well as
with its initial effects on the benthic and demersal continental shelf communities. This final
report presents the main results on macro-infaunal communities obtained after three years of
sampling (2002-2004) in the Galician continental shelf. The sediment of this area is dominated
by fine sands which have a low organic content. No temporal changes that may be attributed
to the impact of the oil spill were observed in the sedimentary variables. The temporal
evolution of the structural parameters of Zone 1 (minimum-impacted area) would not suggest
that they suffered any effect from the oil spill. In Zone 2 (maximum-impacted area) by
contrast, we found an increase in the abundance of one crustacean group (amphipods) in some
stations (10 and 14), a general increase in the total biomass in the 2004 samplings and a
gradual decline in the total abundance and specific richness during the first three samplings of
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ICES BEWG Report 2007
the stations located in stratum B (8, 11 and 14). Zone 3 (moderate-impacted zone) underwent
a progressive decrease in total abundance during the first four samplings and of richness
during the first three samplings in the stations belonging to stratum A (16 and 19). In contrast,
a gradual increase in the abundance of the crustacean group (amphipods) was recorded in the
same stations. Generally speaking, none of the zones showed any major changes in either the
temporal pattern or the structure of the infaunal community. We did not see any marked
increase in opportunistic species or species favoured by the oil spill (i.e. capitellid and spionid
polychaetes). Owing to the lack of previous data, we are unable to confirm whether or not
mortalities have occurred in species that are sensitive to hydrocarbon contamination (i.e.
echinoderms and peracarid crustaceans), although the increasing crustacean populations in
some stations could be related to the oil spill. A more comprehensive account and the first
pages of two relevant publications can be found in Annex 11, Annex 12 and Annex 13.
8.5.5
Gulf of Gdansk benthic habitat spatial mapping
J. Warzocha reported on ongoing benthic studies in the southern Baltic (Polish EEZ).
The major aim of the project is to describe distribution patterns of macrobenthic species and
compare the structure of macrobenthic associations from 1980s and 2000s. The grid of about
350 stations covers the coastal zone from the German border (Pomeranian Bay) to Russia
(Gulf of Gdansk), southern parts of Bornholm and Gotland Basins and Slupsk Furrrow.
Samples were taken with a 25 kg van Veen grab (the same grab as used in the 1980s) and
additionally with a 60 kg van Veen grab, a 200 kg box corer and a dredge fittedwith
underwater video – from 2000 the present day. Results obtained already from the Gulf of
Gdansk, allowed us to distinguish five associations correlated (above halocline) mainly to the
sediment type. The structure of macrofauna on sandy bottom was rather stable – over 20 years
– however, distinct changes were observed in muddy bottom associations, including the
impact of invasive species (such as the spionid - Marenzelleria neglecta).
These studies will be continued as a contribution to a project on habitat mapping which started
at the beginning of 2007, in collaboration with NIVA and is financially supported by
Norwegian Financial Mechanism.
8.5.6
Studies in Portugal
Mirjam Guerra from IPIMAR sent a report on ongoing work in Portugal concerning the WFD
and the restoration and management of biodiversity in the Marine Park Site Arrábida-and also
the biodiversity restoration in the Tagus river estuary. See Annex 9.
9
Assess the effectiveness of any potential performance
indicators in identifying cause-effect relationships based on a
list of indicators prepared by intersessional work (ToR f)
The group updated the list of metrics from the report of the ICES Study Group on Sensitive
and Opportunistic Benthic Species (SGSOBS 2004) (see Annex 14). It was decided that
within the scope of this working group it is difficult to come up with a full review of causeeffect relationships for each of the different indicators. The ideal way of answering this
question would be to organise an intersessional workshop where the majority of indicators, as
defined by the updated list of SGSOBS, can be tested on a series of datasets from different
areas with diverse anthropogenic activity. This workshop should be open to anyone, including
non BEWG members, with knowledge on indicators. The group therefore advises to wait for
the outcome of the Indicator Symposium that will be held in November 2007 in London.
As an example, one of the most tested indices relating to the response to different types of
anthropogenic impacts, AMBI, is incorporated in this report (see below). A similar study on
ICES BEWG Report 2007
| 13
the cause-effect relationship should be performed for all other possible indicators to identify
the most useful indicator for a specific impact.
WGEXT asked the BEWG to interact in the development of useful and consistent indicators to
show the effect of, for example, sand extraction on higher trophic levels. The group agrees it
is necessary to combine effort with and have a better interaction between the different WG’s
(especially WGEXT and WGECO) to cover this subject.
The group also desires to draw attention to the following report concerning the evaluation of
indicators. Thisreport mainly focuses on the impact of fisheries on the ecosystem:
Lutchman I., Rochet M.-J., Tasker M. and J. Brown (2007) INDECO (Development of
indicators of environmental performance of the common fisheries policy) Final analysis and
evaluation of the indicators (www.ieep.eu)
Response of the AMBI to different anthropogenic impacts
This index has been tested by a number of authors, using datasets from different geographical
areas (including all European seas, but also North and South America, North Africa, and
Asia). Their ecological basis (Pearson and Rosenberg’s paradigm) explains how AMBI is able
to respond successfully to very different environmental impact sources, including: drill cutting
discharges; submarine outfalls; harbour and dyke construction; heavy metal inputs;
eutrophication processes; diffuse pollutant inputs; recovery in polluted systems, the impact of
sewage schemes; dredging processes; mud disposal; oil spills; etc. (see Table in Annex 15: ).
It can be seen that AMBI does not respond to physical impacts (e.g. aggregate extraction).
Probably the same can occur with similar impacts, such as fish trawling (but at the moment
there are no data on this subject). On the other hand, some other impacts, such as metal
pollution, have shown contradictory results in different areas. For remaining impacts, the
general response is quite good in terms of gradient detection.
10 Discuss and report on the role of benthos for monitoring
under the WFD and the NATURA 2000 regimes (ToR g)
S. Degraer introduced a document on Benthos ecological status assessment and monitoring
for the Water Framework Directive in the Belgian coastal waters. The document is attached
as Annex 16.
The group discussed ongoing projects concerning WFD matters. Benthos is still the major
component for WFD investigations and assessments. Phytobenthos is only used in few
countries. A. Borja presented Methods used in Europe for the Water Framework Directive and
outlined an Atlantic intercalibration exercise. He showed an international Atlantic scenario
and compared the different metrics in use. Both documents are in Annex 17 and Annex 18.
The table of metric used by different states is given below (Table 10.1)
General discussions on aspects of the AZTI / Spanish programme then commenced. Enquiries
were also made as to how animal dry weights were determined. The method adopted here was
to dry material at 60°C for 24 hours until the weight was constant however, it was pointed out
that in the Baltic, Mytilus material often required up to two weeks for drying . Overall, it was
agreed that the work described by A. Borja was the correct way to proceed with WFD driven
monitoring. It was also pointed out that Germany was trying to develop a new approach to
WFD work which avoided the inclusion of species number and species diversity however a
final decision on this approach was still to be taken. Further to this, Estonia has also adopted a
system of monitoring which employs different metrics to other countries so making
intercalibration exercises very difficult.
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ICES BEWG Report 2007
Estonia
X
Sweden
Denmark
Biomass
X
Finland
X
X
X
X
X
X
X
X
Feeding guilds
OTHERS
Similarity
Simpson
DIVERSITY
Margalef
S
Shannon
Nº
Richness
MEDOCC
Bentix
Sen/opp
BQI
SENSITIVE/OPPORT.
AMBI
MEMBER STATE
Density
Table 10.1. Metrics used for each Member State. Note: Bentix and Medocc are modifications of
AMBI.
X
X
X
Germany
X
X
Netherlands
X
X
X
Belgium
X
X
X
UK
X
X
X
Ireland
X
X
X
France
X
X
X
Spain (Atl)
X
X
X
Portugal
X
X
Spain (Med)
X
X
Italy
X
X
X
Slovenia
X
X
X
Greece
X
Cyprus
X
H. Kautsky enquired whether any work on plants was under way in the WFD programmes and
was assured that the phytobenthos was included in monitoring. Methods developed by the UK
were recently applied along the Spanish Atlantic coast for example. However, this has proved
problematic as the method relies on presence / absence assessments only and lacks a system
for defining the degree of algal cover. Along the Spanish coast the phytobenthos is dominated
by red algae so the UK system always returns a “good” status result. Germany is also
developing a programme for defining the status of the phytobenthos under the WFD while in
the Baltic work is ongoing employing historical data comparisons with current species
occurrence and depth distributions.
The NATURA 2000 regime was then considered. It would appear that very little or no activity
is currently taking place under the NATURA 2000 banner as none of the members of the
BEWG present at the meeting were engaged in any work included in this initiative. Overall,
the question “what is the role of benthos in NATURA 2000” lacks a clear answer. In the
WFD, benthic monitoring is well defined; this is not the case with NATURA 2000.
The Group took note of the report submitted from Portugal and will include it in future
compilations. (Annex 9)
11 Based on the final SGNSBP report discuss further plans for
North Sea benthic surveys (ToR h)
The group recommended that a common survey in 2010 would be ideal but only if externally
funded, otherwise incorporation into national programmes will be required. The planning will
ICES BEWG Report 2007
| 15
be taken up in the BEWG meeting in 2008 and will probably results in a future Study Group.
The final SGNSBP report was submitted to ICES as a CRR and will be available shortly.
12 Discuss recent developments in benthic sampling methodology
with a view on updating the TIMES No. 27 recommendations
(1999) (ToR i)
12.1 TIMES no. 27 recommendations
A subgroup reviewed and updated the TIMES no. 27 recommendations. Recent literature and
developments were incorporated. The new version shall be published after review by other
experts and final editing by ICES.
12.2 Sieving alive or after fixation
S. Degraer gave a presentation on a new paper discussing the difference between sieving
samples alive or after fixation (see first page in Annex 19). The main conclusions of the paper
were that sieving alive negatively impacted all tested diversity measures (S, N1, N2, N∞, H’,
ES100 and J’) and community-dependent relative losses of up to 35% were observed. However,
most trends were ambiguous and statistically non-significant. Community and taxondependent impacts were detected at the level of density. Polychaetes were mainly found to be
negatively impacted by sieving alive (relative losses up to 81%): Interstitial and other small
polychaetes (e.g. Hesionura elongata and Spio filicornis) especiallytend to actively escape
through the sieve meshes (relative loss up to 100%). Next to size, behaviour, the presence of
head appendages, the depth of the sampling stations and sampling season are all believed to
influence the sieving impact. While detailed community composition was affected (ANOSIM
dissimilarity: maximum 85%), no major impact on the differentiation between the investigated
communities was detected. The present study thus demonstrated that combining data,
retrieved with a different sieving procedure can be useful, but its reliability will mainly
depend on the type of questions one wants to answer. In all cases caution at all levels of
ecological organisation is advised.
12.3 Van Veen grab - Hamon grab comparison
I. Moulaert presented some preliminary results on a comparison between samples taken with a
Van Veen grab (VV) and with a Hamon grab (HG). At each of 23 locations on the
Hinderbanken (offshore Belgian continental Shelf) one sample was taken with a Van Veen
grab and one with a Hamon grab. Although the sampling was not designed for a comparison
study, results give an idea of the difference between sampling techniques. As only one sample
with each of the sampling tools was taken, the effects of the patchiness of the area sampled
could not be excluded. Looking at the sample volume a great variation was found for both
sampling tools (from 3 to 13 litres for the HG and 4 to 12 litres for the VV). The median grain
size calculated from a subsample taken from both grabs at every location showed a relatively
good correlation. Total number of individuals, diversity index and number of species were
highly variable. For 50% of the locations the numbers of individuals found were higher in the
HG and in the other half the densities were higher in the VV. The same was found for species
number and diversity. Depth and volume of the sample were not correlated with the
differences found in the biological measures.
The group agreed that further analysis on this data should be undertaken as it would be good
to have an intercalibration exercise between both sampling devices. Extra sampling in
different sediment types might also be interesting.
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ICES BEWG Report 2007
13 Report on the environmental implications of existing off-shore
renewable energy generation installations (wind, wave, tide,
etc.) and make proposals to minimize their negative effects
(ToR j)
There was no new information to be presented at the meeting. A presentation on effects of
Wind farm installations was given on the BSH symposium in Hamburg 2006. In Germany
Pilot Wind farms are being erected in the German Bight and the environmental results are
awaited eagerly.
14 Any other business
14.1 Upcoming Symposia
14.1.1 42 nd European Marine Biology Symposium (EMBS)
The 42nd European Marine Biology Symposium will be held in Kiel, Germany 27–31 August
2007. The symposium’s website is at http://www.embs42.meeresbiologie.at/home.htm.
14.1.2 Conference of the Estuarine Research Federation 2007 (ERF 2007)
The Conference of the Estuarine Research Federation 2007 will be held in Providence, Rhode
Island, U.S. 4-8 November 2007. The symposium’s website is at http://erf.org/erf2007/. A
theme session Assessing ecological integrity using multiple indices and ecosystem
components is organized, chaired by A. Borja and J. Ananda Ranasinghe.
14.1.3 10 th International Conference on Shellfish Restoration (ICSR)
The 10th International Conference on Shellfish Restoration (ICSR) will be held in Vlissingen,
The Netherlands, 12–16 November 2007. This year’s title is “Innovation in the exploitation
and management of shellfish resources”. (http://www.icsr2007.wur.nl)
14.1.4 ICES Symposium on Environmental Indicators: Utility in Meeting
Regulatory Needs
The ICES Symposium on Environmental Indicators will be held in London, UK, 20-23
November 2007. The program and online registration will be available on 15 May 2007 at the
symposium website. (http://envind2007.benthos.be/)
14.2 Workshop/symposia proposals
Workshop on the role of the need of phytobenthic communities in ICES waters, including
epiflora and fauna, population dynamics, WFD, ICZM and socio-economic valuation. Chaired
by H. Kautsky.
Workshop on the performance testing of indicators. Chaired by I. Moulaert.
14.3 BEWG website
H. Hillewaert presented an update of the group’s website at http://www.bewg.be. Members
were called upon to provide links to project websites or other sites of interest to the Working
Group.
ICES BEWG Report 2007
| 17
14.4 LYYN T38 Real time image enhancer
H. Rumohr mentioned a video tool where the visibility enhancement is done in real-time in a
live video stream, which also can be used on stored material. An interesting application can be
to enhance the feed from a live video system, e,g. in a ROV.
(http://www.lyyn.com/products/T38.html)
LYYN T38 Real time image enhancer
14.5 Taxonomic help
The group gave taxonomic ID help to undetermined species from Belgian samples and was
proving its function as a team of colleagues who share their expertise for the mutual benefit.
15 Adoption of report
After review and discussion the group adopted the last version of the draft report
16 Closing of the meeting
The Chair thanked the local host for their generous hospitality and the interesting excursion to
the east-Frisian country and moors. He also thanked the contributors for their input especially
the rapporteurs and the editing rapporteur and closed the meeting on Friday, 13:00 hours.
18 |
ICES BEWG Report 2007
Annex 1: Lis t of p art i c ipa n t s
NAME
Ingeborg de Boois
Ángel Borja
Steven Degraer
Karel Essink
Hans Hillewaert
Hans Kautsky
Ingrid Kröncke
Ine Moulaert
Hermann Neumann
Santiago Parra
Eike Rachor
Henning Reiss
ADDRESS
IMARES
P.O.Box 68
1970 AB IJmuiden
Netherlands
AZTI
Herrera kaia, Portualde
z/g
20110 Pasaia
(Gipuzkoa)
Spain
UGent
Krijgslaan 281 – S8
B-9000 Gent
Belgium
Hooiweg 119
9765 EE Paterswolde
Netherlands
ILVO-Fisheries
Ankerstraat 1
B-8400 Oostende
Belgium
Department Systems
Ecology
Stockholm University
10691 Stockholm
Sweden
Senckenberg Institute
Südstrand 40
D-26832
Wilhelmshaven
Germany
ILVO-Fisheries
Ankerstraat 1
B-8400 Oostende
Belgium
Senckenberg Institute
Südstrand 40
D-26832
Wilhelmshaven
Germany
Centro Oceanográfico
de La Coruna
Muelle de las Animas
s/n
Apdo 130
E-15001 La Coruña
Spain
Alfred-Wegener-Institut
Foundation
for Polar and Marine
Research
P.O. Box 12 0161
D-27515 Bremerhaven
& BfN - Vilm
Germany
University of
Groningen – Dept. Of
Marine Ecology and
Evolution
Kerklaan 30
9750 AA Haren
Netherlands
PHONE/FAX
Phone:
+31 255 564696
Fax:
+31 255 564644
Phone:
+34 943004800
Fax:
+34 943004801
EMAIL
ingeborg.deboois@wur.nl
Phone:
+32 (0)9 264 8522
Fax:
+32 (0)9 264 8598
Phone:
+31 50 3090141
steven.degraer@ugent.be
Phone:
+32 59 569832
Fax:
+32 59 330629
Phone:
+46 8 164244
hans.hillewaert@ilvo.vlaanderen.be
Phone:
+49 4421 9475250
Fax
+49 4421 9475299
ingrid.kroencke@senckenberg.de
Phone:
+32 59 569847
Fax:
+32 59 330629
Phone:
+49 4421 9475267
ine.moulaert@ilvo.vlaanderen.be
Phone:
+34 981 205362
Fax:
+34 981 229077
santiago.parra@co.ieo.es
Phone:
+49 471 4831/1310
eike.rachor@awi.de
Phone:
+31 503 63 2243
h.reiss@rug.nl
aborja@pas.azti.es
karelessink@hetnet.nl
hassek@ecology.su.se
hneumann@senckenberg.de
ICES BEWG Report 2007
NAME
Mike Robertson
Heye Rumohr
(Chair)
Sabine Schückel
Ulrike Schückel
Sandra Vöge
Jan Warzocha
| 19
ADDRESS
Environmental Impact
Group
FRS Marine Laboratory
PO Box 101
Aberdeen
UK AB11 9DB
Leibniz Institute for
Marine Reseach
IFM-GEOMAR
Düsternbrooker Weg 20
D-24105 Kiel
Germany
Senckenberg Institute
Südstrand 40
D-26832
Wilhelmshaven
Germany
Senckenberg Institute
Südstrand 40
D-26832
Wilhelmshaven
Germany
Senckenberg Institute
Südstrand 40
D-26832
Wilhelmshaven
Germany
Sea Fisheries Institute
ul. Kollataja 1
PL-81-332 Gdynia
Poland
PHONE/FAX
Phone:
+44 1224 295433
Fax:
+44 1224 295511
EMAIL
M.R.Robertson@marlab.ac.uk
Phone:
+49 431 600 4524
Fax:
+49 431 600 1671
hrumohr@ifm-geomar.de
Phone:
+49 4421 9475251
sschueckel@senckenberg.de
Phone:
+49 4421 9475251
uschueckel@senckenberg.de
Phone:
+49 4421 9475253
Sandra.voege@senckenberg.de
+48 58 621 71 95
+48 58 620 28 31
janw@mir.gdynia.pl
20 |
ICES BEWG Report 2007
Annex 2: BEW G Ag enda
Wilhelmshaven, Germany, 23–27 April 2007
Start 23.04, 13:00
Opening & Local Organisation
•
Appointment of Rapporteur;
•
Terms of Reference;
•
Adoption of Agenda.
(ToRs ranked according importance for ICES)
Report on ICES meetings and other meetings of interest
•
ASC 2006 (Maastricht) / ICES Annual Report for 2006;
•
Marine Habitat Committee, Maastricht 2006;
•
ACE , Maastricht 2006;
•
ACME Maastricht 2006;
•
STGQAB (?);
•
WGMHM;
•
WGEXT;
•
MarBEF;
•
WGECO.
TOR e) review and consider recent developments in ongoing benthos research
in Europe
•
Cooperative studies;
•
Benthos and fisheries;
•
Benthos of soft sediments;
•
Benthos of rocky substrates;
•
Other studies.
TOR a ) assess and report on changes in the distribution, population
abundance and condition of benthic invertebrates in the OSPAR maritime
area in relation to changes in hydrodynamics and sea temperature (further
details on the interpretation and handling of this ToR will be provided by
ACE);
TOR b ) assess and report on the extent to which the changes reported in (a)
can reliably be attributed to changes in hydrodynamics and sea temperature
(further details on the interpretation and handling of this ToR will be
provided by ACE);
TOR c ) assess and report on the evidence on which the nomination of
Seagrass Cymodocea meadows for the OSPAR List of Threatened and/or
Declining Species and Habitats is based [Note: this Term of Reference only has
to be addressed if this request has not been fulfilled by an ad-hoc group in
advance of the Expert Group meeting. Whether an ad-hoc group will be
required can only be decided after further consultations with OSPAR. based on
input from OSPAR MASH which meets in October. The ACE Chair will inform the
Chair on the outcome of these discussions in November 2006].
TOR d ) discuss and report on quality assurance and control guidelines for
sampling and analytical practices for benthos;
ICES BEWG Report 2007
TOR f ) assess the effectiveness of any potential performance indicators in
identifying cause-effect relationships based on a list of indicators prepared
by intersessional work;
TOR g ) discuss and report on the role of benthos for monitoring under the
WFD and the NATURA 2000 regimes;
TOR h ) based on the final SGNSBP report discuss further plans for North Sea
benthic surveys;
TOR i ) discuss recent developments in benthic sampling methodology with a
view on updating the TIMES No. 27 recommendations (1999);
TOR j ) report on the environmental implications of existing off-shore
renewable energygeneration installations (wind, wave, tide, etc.) and make
proposals to minimize their negative effects
Any other business
•
further theme sessions
•
Upcoming symposia etc
Recommendations and Action List
•
Recommendations for next years meeting (2008)
•
Recommendations for Theme Sessions/ Symposia
•
Action List
Adoption of the report (due 15.5.2007)
Closing of the meeting
Local organisation and schedule
•
Morning session 9:00–13:00 coffee break 10:30–11:00
•
Lunch (in-house catering) 13:00–14:00
•
Afternoon session 14:00–18:00 coffee break 15:30–16:00
| 21
22 |
ICES BEWG Report 2007
Annex 3: B E W G T e r m s o f R e f e r e n ce 2 0 0 6
2006/2/MHC10 The Benthos Ecology Working Group [BEWG] (Chair: H. Rumohr) will
meet in Wilhelmshaven, Germany, from 23–27 April 2007 to:
a)
b)
c)
d)
e)
f)
g)
h)
i)
j)
assess and report on changes in the distribution, population abundance and
condition of benthic invertebrates in the OSPAR maritime area in relation to
changes in hydrodynamics and sea temperature (further details on the
interpretation and handling of this ToR will be provided by ACE);
assess and report on the extent to which the changes reported in (a) can reliably
be attributed to changes in hydrodynamics and sea temperature (further details on
the interpretation and handling of this ToR will be provided by ACE);
assess and report on the evidence on which the nomination of Seagrass
Cymodocea meadows for the OSPAR List of Threatened and/or Declining
Species and Habitats is based
discuss and report on quality assurance and control guidelines for sampling and
analytical practices for benthos;
review and consider recent developments in ongoing benthos research in the
ICES area;
assess the effectiveness of any potential performance indicators in identifying
cause-effect relationships based on a list of indicators prepared by intersessional
work;
discuss and report on the role of benthos for monitoring under the WFD and the
NATURA 2000 regimes;
based on the final SGNSBP report discuss further plans for North Sea benthic
surveys;
discuss recent developments in benthic sampling methodology with a view on
updating the TIMES No. 27 recommendations (1999);
report on the environmental implications of existing off-shore renewable energy
generation installations (wind, wave, tide, etc.) and make proposals to minimize
their negative effects.
BEWG will report by 15 May 2007 to the attention of the Marine Habitat Committee and
ACE.
Supporting Information
PRIORITY:
The current activities of this Group will lead ICES into issues related to the
ecosystem affects of fisheries, especially with regard to the application of the
Precautionary Approach. Consequently, these activities are considered to have a
very high priority.
SCIENTIFIC
Action Plan 1.2.1, 2.2.1, 2.13, 4.12, 2.11
Term of Reference a, b, c)
These ToRs are set to provide information for a request from OSPAR.
Term of Reference d)
This work is in response to the MOU with OSPAR and HELCOM for the
provision of advice on quality assurance of biological measurements. It will be
augmented when necessary with specific annual requests from HELCOM and/or
OSPAR.
Term of Reference e) This is a prerequisite for the scientific information status of
the group
Term of Reference f) This is in response to ongoing OSPAR requests and in
perspective of the coming ICES Symposium on Indicators in November 2007. This
is also in response to a request from ACME. ICES is moving towards providing
scientific advice for the integrated management of all human activities that affect
marine waters. Information on the quantity and quality of habitat and the health of
marine ecosystems will be essential to the achievement of this goal.
Term of Reference g) Benthos will be a major component in the monitoring
regimes of the European WFD and the NATURA 2000 network of nature reserves.
JUSTIFICATION
AND RELATION
TO ACTION PLAN:
ICES BEWG Report 2007
| 23
The BEWG is prepared to evaluate national plans of monitoring and especially
how far the comparability is guaranteed to arrive at scientifically suited long-term
data sets.
Term of Reference h) The SGNSBP is a major research activity of the BEWG
and the basis for the discussion of future joint activities in the BEWG
Term of Reference i) This is a needed update of the methods recommendations
discussed and formulated 10 years ago.
Term of Reference j) There is a growing need for a harmonized approach to
benthic studies in view of the rapid expansion of the interest in off-shore wind
energy and other forms of energy generation off-shore. It will provide further
advice in response to the OSPAR.
RESOURCE
REQUIREMENTS:
The research programmes which provide the main input to this group are already
underway, and resources are already committed. The additional resource required
to undertake additional activities in the framework of this group is negligible.
PARTICIPANTS:
The Group is normally attended by some 20–25 members and guests.
SECRETARIAT
FACILITIES:
None.
FINANCIAL:
No financial implications.
LINKAGES TO
There are linkages to ACME and ACE.
ADVISORY
COMMITTEES:
LINKAGES TO
WGMHM, WGEXT, MHC
OTHER
COMMITTEES OR
GROUPS:
LINKAGES TO
OTHER
ORGANIZATIONS:
None
24 |
ICES BEWG Report 2007
Annex 4: Dra ft res ol ut io ns for n ext ye ar
The Benthos Ecology Working Group [BEWG] (Chair: H. Rumohr) will meet in Torre
Grande, Sardinia, Italy, from 21–25 April 2008 to:
a)
b)
c)
d)
e)
f)
plan the next North Sea Benthos Project 2010;
review and consider recent developments in ongoing benthos research in the
ICES area;
discuss and report on new methods for sampling and analytical practices for
benthos including electronic ones;
report and discuss possible climate enforced changes in the benthos in the
Mediterranean compared to ICES waters;
consider the Mediterranean phytobenthos in relation to Northern European
environments;
report and discuss on the outcome of the workshop on Benthos Related
Environmental Metrics (WKBEMET).
BEWG will report by 15 May 2008 for the attention of the Marine Habitat Committee and
ACME.
Supporting Information
PRIORITY:
SCIENTIFIC
JUSTIFICATION AND
RELATION TO ACTION
PLAN:
JUSTIFICIATION OF
VENUE (IN A NONICES MEMBER
COUNTRY)
The current activities of this Group will lead ICES into issues related to the
ecosystem affects of fisheries, especially with regard to the application of the
Precautionary Approach. Consequently, these activities are considered to have
a very high priority.
Action Plan 1.2.1, 2.2.1, 2.13, 4.12, and 2.11
Term of Reference a)
This project is one of the central activities throughout the existence of the
group and will provide valuable data with relevance to OSPAR and EU
requests
Term of Reference b) This is a prerequisite for the scientific information
status of the group
Term of Reference c) This a prerequisite for update of method
recommendations and Quality Control routines
Term of Reference d) This reflects ICES coperation with the mediterranean
CIESM. Input is also awaited from colleagues from the Mediterranean.
Term of Reference e) This continues the attempts to include phytobenthos in
ICES benthos work and make the results ready for potential OSPAR requests.
It will shed some light on pan-european environmental dynamics
Term of Reference f) This a consquence of the proposed workshop on the
performance testing of environmental metrics.
1) If the ToRs of the group explicitly limit its activities to the ICES area meetings
should normally be held in an ICES member country.
This is not the case for BEWG.
2) The host country should normally be linked to ICES (member or
affiliate country or co-sponsor of the EG).
Italy is not an ICES affiliate but is an EU country and member of CIESM a
potential future partner of ICES.
3) The host institute should include scientists who are already
members of the EG.
This is not the case, the contacts are from earlier IOC group meetings in Torre
Grande and from EU sponsored meetings under MARBEF.
4) The inviting country should benefit from hosting the meeting.
This is obvious from the agenda and from the fact of the invitation.
5) ICES in general and the EG in particular should benefit from
the expertise and knowledge of the host country or region. Specifically where the
response to the EG ToRs can be enhanced by the proposed hosts.
This is the case and is part of the agenda in TOR d and e. This is a reaction to
research in consquences of climate change and global warming and the potential
ICES BEWG Report 2007
| 25
consequences of this. This will be future requests for advice by OSPAR; EU and
HELCOM.
6) The EG should not have held a meeting in a non-member country
during the last three years.
BEWG met 2005 in Copenhagen, 2006 in Crete (Greece is an ICES affiliate) and
2007 in Germany.
7) The EG should evaluate the cost implications of the venue
choice. This should consider what additional cost that would be incurred by the
usual attendees, and particularly ICES members. It should also evaluate whether
the choice would limit attendance by these members.
There are no additional cost implications. On the contrary, Sardinia is a cheep
destination compared to other destinations in Europe and especially in Canada
and the US. This is because of cheap charter flights anf cheap accommodation
early in the year. It should be noted here that meetings at ICES Headquarters are
under the most expensive venues in Europe. This choice of venue does not limit
attendance by members it enforces participation of experts because of its
attractive character and the chance to meet new colleagues .
RESOURCE
REQUIREMENTS:
PARTICIPANTS:
SECRETARIAT
FACILITIES:
FINANCIAL:
LINKAGES TO
ADVISORY
COMMITTEES:
The research programmes which provide the main input to this group are
already underway, and resources are already committed. The additional
resource required to undertake additional activities in the framework of this
group is negligible.
The Group is normally attended by some 20–25 members and guests.
None.
No financial implications.
There are linkages to ACME and ACE.
LINKAGES TO OTHER
COMMITTEES OR
GROUPS:
WGMHM, WGECO, WGEXT, MHC
LINKAGES TO OTHER
ORGANIZATIONS:
None
26 |
ICES BEWG Report 2007
Two workshop recommendations
BEWG recommends the organisation of a Workshop on Benthos Related Environmental
Metrics:
The Workshop on Benthos Related Environmental Metrics [WKBEMET] (Chair: I.
Moulaert, Belgium) will meet in Oostende, Belgium from 11–14 February 2008 to:
a)
b)
c)
discuss the outcomes of the “Symposium on "Marine Environmental Indicators:
Utility in Meeting Regulatory Needs” held in November 2007 in London and of
the Intercalibration working group for the WFD. Look for the gaps in the
knowledge of the applicability and performance of different indicators to the
impacts of human-induced activities and changes in ecological state;
test the applicability of different indicators using multiple datasets from a wide
range of regions;
use multiple datasets to test the performance of different indicators to human
induced activities and changes in ecological state and to assess the effectiveness
of performance indicators in identifying cause-effect relationships.
WKBEMET will report by 15 April 2008 for the attention of BEWG, MHC and ACME.
Supporting Information
PRIORITY:
SCIENTIFIC
JUSTIFICATION AND
RELATION TO ACTION
PLAN:
RESOURCE
REQUIREMENTS:
PARTICIPANTS:
SECRETARIAT
FACILITIES:
FINANCIAL:
LINKAGES TO
High.
The main aim of this workshop is (1) to relate a list of indicators to the
impacts of human-induced activities and changes in ecological state and (2) to
assess the effectiveness of any potential performance indicators in identifying
cause-effect relationships.
None.
People are invited with experience in parameter testing and with access to
benthos data sets.
None
None
ACME
ADVISORY
COMMITTEES:
LINKAGES TO OTHER
COMMITTEES OR
GROUPS:
BEWG
LINKAGES TO OTHER
ORGANIZATIONS:
Cooperation with MarBEF is sought through the VLIZ in Ostende.
Furthermore, BEWG recommends a workshop to be held in 2008 on the role of phytobenthic
communities in ICES waters, including epiflora and fauna, exploring population dynamics,
connections with WFD, ICZM and socio-economic valuation:
the Workshop on the role of phytobenthic communities in ICES waters [WKPHYT] (CoChairs: Hans Kautsky, Sweden, N.N. Country) will meet in [venue to be decided] spring 2008
to:
a)
Explore and discuss the role of phytobenthic communities in ICES waters,
including epiflora and fauna;
b ) document the population dynamics and annual cycles of phytobenthos
communities on a regional scale;
ICES BEWG Report 2007
| 27
c ) elaborate connections with WFD and the role of phytobenthos in ICZM and its
socio-economic valuation;
d ) Finalize the ICES TIMES draft on Phytobenthos sampling methodology.
WKPHYT will report by 15 May 2008 for the attention of the Marine Habitat Committee,
BEWG, WKBEMET, and WGMHM.
Supporting Information
PRIORITY:
SCIENTIFIC JUSTIFICATION
AND RELATION TO ACTION
PLAN:
RESOURCE
REQUIREMENTS:
PARTICIPANTS:
SECRETARIAT FACILITIES:
FINANCIAL:
LINKAGES TO ADVISORY
COMMITTEES:
The work of the Group is essential if ICES is to progress the
developments of techniques in fish stock assessment.
The work done within BEWG has been diverse and has included
sampling methodology and all aspects of benthos ecology. Since some
years phytobenthos has been included in the remits of the Committee
since phytobenthos has a natural and logical link with the normally
treated zoobenthos part of, benthos ecology. Phytobenthos forms not
only the shelter for coastal fish and invertebrate epifauna but is also
increasingly an object of harvesting and specialized usage as a valued
natural material and thus a source of income for the coastal
population.The new WKPHYT will focus on the phytobenthos in the
benthos area , a field that has been neglected in ICES work so far.
Recent .OSPAR requests asked especially for phytobenthos expertise on
a european scale that could not easily provided. This is an act of
scientific capacity builiding for ICES. Both methodology and scientific
contents need to be updated and collectively documented as work basis
in the mentioned contact groups.
No specific resource requirements beyond the need for members to
prepare for and participate in the meeting.
people from the benthos community and new experts from the
phytobenthos scene
none specific
None specific.
A close link with ACME activities.
LINKAGES TO OTHER
COMMITTEES OR GROUPS:
Links to BEWG and WGICZM
LINKAGES TO OTHER
ORGANIZATIONS:
ICES will seek widened participation for this group from the Baltic
(BMB) and from other North Atlantic and North American States
Action list
•
Santi - Long term macrofauna communities in La Coruña Bay;
•
Hasse - Final draft of TIMES document on phytobenthos sampling;
•
Ingrid - Deep sea research in the eastern Mediterranean;
•
Mike - Final report on HAPMAP + other work;
•
Angel - Integrity of ecological assessments;
•
Ine, Hans - Workshop report, intercalibration + other work;
•
Sylvana, Ine, Angel - finalize dredging paper;
•
Henning (Hubert) - Study group on biodiversity + ecosystem management;
•
Jan - Distribution and dynamics of macrozoobenthos in the Baltic.
28 |
ICES BEWG Report 2007
Annex 5: B e n t h o s a n d c l i m a t e c h a n g e i n t he B a y o f B i s c a y
By Angel Borja (AZTI-Tecnalia)
The distribution of many benthic species, including macroalgae, molluscs and arthropods, was
studied by Alcock (2003) along the Bay of Biscay, between the end of 19th century and 20002001. He determined some shifts northwards and southwards, depending on the warm and
cool periods, during the 20th century, and several examples were shown for species such as
Fucus spiralis, Pelvetia canaliculata, etc.
Taking into account this evolution and the IPCC scenarios of temperature increase for next 50
years, Alcock (2003) modelled the future shift of some benthic species in the Bay of Biscay,
North Sea, and Norwegian Sea. In this presentation, the predicted shifts for Balanus
perforatus, Chthamalus montagui, Patella rustica and Pollicipes Pollicipes were presented.
These scenarios can be useful, for future monitoring programmes, in order to check the
northwards migration of benthic species, due to climate change.
Some studies, undertaken in the Basque coast, were presented. Hence, the relationships
between NAO and benthic diversity and precipitation and richness, in the Nervion estuary,
were presented. Long term series of Gelidium sesquipedale biomass have shown a close
relationship with irradiance (Borja et al., 2004). Finally, strong relationships between wave
energy and biomass, abundance and cover of Pollicipes Pollicipes, have been found in the
area (Borja et al., 2006).
Taken into account the predicted increasing NAO values, for the next 50 years, some
scenarios have been built for the Basque coast. This fact will lead to an increase of
northwesternly wind circulation over the area, and, consequently, to an increase of wave
energy and clouds. Hence, there are possibilities of an increase of Pollicipes biomass, a
decrease of Gelidium biomass, and a reduction of richness and diversity of benthic
populations.
ICES BEWG Report 2007
Annex 6: Re d Lists in Ger m any
Table 1 Categories of species
Table 2 Criteria to assign species
Table 3 Some of the taxa considered in this study.
| 29
30 |
ICES BEWG Report 2007
Annex 7: Re port o n be nt h o s c ha ng e s i n t he O S PA R a rea
Introduction
Request
The BEWG was requested “to prepare an assessment of what is known of the changes in the
distribution and abundance in the OSPAR maritime area in relation to changes in
hydrodynamics and sea temperature. The assessment should look at ecologically indicative
species, including the threatened and declining species identified by OSPAR, for which
adequate time series data exist, in order to assess to what extent there have been changes in
distribution, population and condition of species going beyond what might have been expected
from natural.”
Approach and limitations
In this report, we have selected studies of temporal trends covering all or most of the period
between 1980s and present, especially those of a regular rather than intermittent nature.
Collectively, these have the potential to throw light on broader-scale influences on the
macrobenthic communities.
The interpretation of long-term changes in the benthos is difficult because it is difficult to
detect distinct effects of a single impact, since eutrophication and fisheries might cause rather
similar effects like increasing abundance and biomass, whereas species numbers might drop
under fisheries impact due to the damage of long living species. The same might be true for
sand and gravel dredging.
Available information
A compilation (not necessarily complete) of long-term studies in the OSPAR regions is
presented in Table A7.1. As can be seen from this table there is a focus of relevant studies on
region II (North Sea). Therefore, our main discussion will refer to studies of this region.
ICES BEWG Report 2007
| 31
Table A7.1. Compilation of metadata of long-term series and long-term comparisons of benthic
fauna in the OSPAR regions.
SOFT-BOTTOM INFAUNA
OSPAR
Time scale
References
region
German Bight (Ziegelmeier)
II
1950s–1970
(Ziegelmeier, 1978)
Dogger Bank
II
1951–52, 1985–87,
1996–98
(Wieking and Kröncke, 2001)
German Bight (AWI)
II
1965– present
(Schroeder, 2003)
Skaggerak
II
1970–1998
--
Northumberland
II
1971–present
(e.g. Frid et al., 1996)
NOR oil platform monitoring
II
1973–present
--
UK oil platform monitoring
II
1977–1998
--
Norderney (Senckenberg)
II
1978–present
(Kröncke et al., 2001)
Norderney (Niedersachsen)
II
1976–1999
--
Northern North Sea
II
1981–1986
--
Dutch oil platform monitoring
II
1985–1993
(Daan and Mulder, 1995)
NSBS, NSBP
II
1986, 2000
(e.g. Rees et al., 2002)
German inshore monitoring
II
1987– present
--
Danish monitoring program
II
1989–1999
--
Dutch monitoring North Sea (BIOMON)
II
1991– present
(e.g. Daan and Mulder, 2001)
Dutch Continental Shelf (MILZON)
II
1988–1993
(Holtmann, 1994)
Shellfish monitoring North Sea
II
1995– present
(Craeymeersch and Perdon, 2004)
Shellfish montoring Waddensea
II
1991–present
(Craeymeersch and van Stralen, 2004)
Dutch monitoring Waddensea
II
1980s–present
(e.g. Dekker and de Bruin, 2001)
Gullmarsfjord
II
1983– ?
--
Danish monitoring Skagerrak
II
? –2004
(Ærtebjerg et al., 1998)
German Bight Transect
II
1990–present
(Kröncke and Rachor, 1992)
Creutzberg Dutch North Sea sampling
(NIOZ)
II
>1970
--
German Bight (GB), surveys
II
1923, 1965, 1975, 2000
(Rachor and Nehmer, 2003)
GB Borkum Riffgrund
II
1967–72, 1996, 1999
(Rachor and Nehmer, 2003)
Belgian Continental Shelf
II
1979–present
--
Disposal Sites, Northumberland (UK)
II
1984–present
(Rees et al., 2003)
Disposal Sites, Thames (UK)
II
1985–present
--
Uk National Marine Monitoring Programm II
1995–present
Anon. 2004
La Coruna Bay, NW Spain
IV
1982–present
(López-Jamar et al., 1995)
Bay of Biscay (Basque coast, Nervion
estuary)
IV
1989–present
(Borja et al., 2006)
Bay of Biscay (Basque coast and estuaries) IV
1995–present
(Borja et al., 2004)
van Mijenfjord
I
1980, 2000–present
--
Svalbard fjords
I
1990s–present
--
western Barents Sea
I
1980, 1992, 2005
--
32 |
ICES BEWG Report 2007
Table 1. Continued.
SOFT-BOTTOM EPIFAUNA
OSPAR
Time scale
References
region
Shellfish monitoring North Sea
II
1995–present
(Craeymeersch and Perdon, 2004)
Shellfish montoring Waddensea
II
1991–present
(Craeymeersch and van Stralen, 2004)
MAFF
II
1980–1986
--
NSBS
II
1986
(Duineveld et al., 1991)
ZISCH
II
1987–1988
--
EU (Biodiversity, MAFCONS)
II
1986–present
(Zühlke et al., 2001)
Epibenthos (GSBTS)
II
1998–present
(Ehrich et al., 2007)
Creutzberg's trawl surveys North Sea II
1970s–1980
Creutzberg & van Noort reports 1–10
German Bight, Epi AWI, incl. Stones II
1999–present
(Rachor and Nehmer, 2003)
Belgian Continental Shelf
II
1979–present
--
South-West Netherlands
II
1985–2004
--
Helgoland
II
1987–1991, 2000–2004 --
HARD-BOTTOM EPIFAUNA
Danish monitoring on stone reefs
II
1990–2004
--
Helgoland (BAH-AWI)
II
last 150 years
(Franke and Gutow, 2004)
Svalbard fjords
I
1980s–2006
--
Changes in benthos
Abundance, species number and biomass may be affected by several parameters such as
temperature and hydrodynamics (Figure A7.1). Temperature itself will influence the
distribution of northern and southern species. Primary production is influenced by temperature
and the direction and flow of marine currents (e.g. via the transport of nutrients). The amount
of primary production reaching the benthic system strongly influences the trophic structure of
the communities in question. Hydrodynamics (e.g. current velocities, stratification of water
layers, wave climate) determine the transport of larvae and influence the sediment
composition, which reflects food availability. Thus, changes in both factors will affect species
composition with regard to sediment preference and the trophic structure of the benthic
communities.
It is known that sea temperature and hydrodynamics seldom change independently and are in
most instances are expressions of climatic and weather conditions (Kröncke et al., 1998;
Planque and Taylor, 1998; Dippner and Kröncke, 2003). Many recent studies on changes in
the pelagic as well as the benthic system in the North Atlantic describe large scale climatic
variability by means of the North Atlantic Oscillation (NAO) index (for a review see
Drinkwater et al., 2003). The effects on benthos may be seen with a delay of up to several
years (Kröncke et al., 1998; Tunberg and Nelson, 1998; Schroeder, 2003; Gröger and
Rumohr, 2006; Rees et al., 2006).
Measures of large-scale climatic changes, such as the NAO Index, are often more effective
correlates than locally-measured variables (e.g., temperature) and better integrate the
complexities of interactions between local climate and ecological processes (Hallett et al.,
2004).
ICES BEWG Report 2007
| 33
NAO
temperature
(SST, bottom )
primary
production
species
composition
direction and flow
of marine currents
larval
supply
trophic
structure
height of waves
(WWS )
sediment composition
food availability
species
composition
trophic
structure
macrozoobenthos
Figure A7.1 Conceptual model of the links between NAO and benthic communities (after Wieking
and Kröncke, 2001).
From the above information it is evident that it is hardly feasible to effectively discriminate
between effects of temperature changes and changes in hydrodynamics. The following
chapters give a presentation of to what extent climate changes (as indicated by the NAOI), and
changes in hydrodynamics and sea temperature can be related to changes in benthos.
Changes in benthos related to climatic factors
NAOI
Many recent studies on changes in the benthic system in the North East Atlantic describe large
scale climatic variability by means of the NAOI (Drinkwater et al., 2002). Significant
correlations between NAOI and changes in abundance and biomass were found in the western
North Sea (Rees et al. 2006), in the Skagerrak (Tunberg and Nelson 1998), the western Baltic
(Gröger and Rumohr, 2006), at the Dogger Bank (Wieking and Kröncke, 2001), in the
German Bight (Kröncke et al., 1998; Schroeder, 2003), in all cases with a time lag from
months to years.
From these studies we know that in general a negative NAOI is associated with lower than
average abundance and biomass, while a positive NAOI is often associated with higher than
average values. According to recent insights the NAOI shows a long-term increasing trend
with internal oscillations. This increasing trend would therefore mean increasing trends in
abundance, species number and biomass of benthos. In specific areas deviations from general
“rule” may occur due to specific local forcing (e.g. Tunberg and Nelson, 1998).
However, this pattern can be different depending on the location within the OSPAR region,
because For example, in the south of the Bay of Biscay, high NAO values produce lower
diversities and negative values produce high diversity values (Borja, com. pers.).
Hydrodynamics
Large-scale hydrodynamic changes were found for the North Sea. Oceanographic models by
Siegismund (2001) and Siegismund and Schrum (2001) showed differences between in the
current regimes of the North Sea between the 1980s and 1990s due to the increasing inflow of
Atlantic water masses mainly through the Fair Isle Current and stronger southwesterly winds.
34 |
ICES BEWG Report 2007
Hydrographic changes in the Baltic are to a large extent related to inflow of North Sea water
masses through the Danish Straits (e.g. Hänninen et al., 2000).
The variable inflow of Atlantic water into the North Sea influenced the plankton and fish
(Ehrich and Stransky, 2001; Reid and Edwards, 2001; Reid et al., 2003).
For the benthos however, only little information is available. This information consists mainly
of inferred causal relationship between the benthos and NAO driven hydrodynamics.
Witbaard (1996) assumed that the variations in the ESAI (East Shetland Atlantic Inflow) and
the Dooley Current influenced the strength of the eddy system over the Fladen Ground and
consequently the accumulation of material in its centre and the eddy mediated food-supply
(growth variations of the bivalve Arctica islandica from the Fladen Ground).
Hagberg et al. (2004) suggest a possible relationship between the NAO and the benthos off
Northumberland due to the strong connections between the inflow of North Atlantic Water to
the North Sea and the NAO.
Wieking and Kröncke (2001) found that the benthic communities along the northern slope of
the Dogger Bank were strongly affected by increasing wind stress and stronger currents at the
northern slope of the Dogger Bank in the 1990s compared to the 1980s. Factors which are also
influenced by the positive NAO index during the 1990s (Siegismund, 2001; Siegismund and
Schrum, 2001). Changes in larval supply, food availability and sediment composition caused
by resuspension of fine material lead to a decrease in species occurring on fine sand (e.g.
Ophelia borealis) compared to the 1980s, whereas abundances and total number of species
preferring coarser sediment (e.g. Echinocyamus pusillus) increased in the 1990s.
In the Bay of Biscay, Borja et al. (2006) have found strong relationships between wave energy
and biomass, abundance and cover of Pollicipes Pollicipes in hard-bottom communities
Consequently, increasing NAO values (as predicted by Cook et al. (2005), for the next 50
years), could lead to an increase of northwesterly wind circulation over the area, and to an
increase of wave energy (as predicted by several models for the area). Finally, this can lead to
an increase of Pollicipes biomass.
Laine et al. (1997), like many others, describe effects on the benthos in the Baltic Sea. Here
variations in North Sea water inflow influence the oxygen concentration in deep waters of the
basins and thus the benthos.
Temperature
In this chapter we present a few studies available which refer directly to the influence of sea
temperature on the benthos.
Well known is the structuring effect of winter temperatures on benthic communities living in
relatively shallow waters. Fromentin and Ibanez (1994) showed that Abra alba communities
in the Southern Bight responded to mild winters between 1977 and 1991 with maximum
densities.
Short-term effects of cold winters on intertidal and subtidal benthic communities include
increased mortality among adults and increased recruitment success among e.g. bivalves
(Ziegelmeier, 1970; Buchanan et al., 1978; Beukema, 1979; Schroeder, 2003; Reiss et al.,
2006) Essink et al. 2006). Beukema (1990; 1992) and Bhaud et al. (1995) expected for the
future a shift in species composition towards a more diverse, warmer water fauna also for the
intertidal and shallow coastal waters, if the trend of increasing water temperature continues.
Also summer temperature has effects on benthic communities. In the Wadden Sea, the Pacific
oyster (Crassostrea gigas) increased considerably in abundance after 2000, causing the partial
disappearance of intertidal beds of Mytilus edulis, at the same time creating new oyster reefs
ICES BEWG Report 2007
| 35
with an approximately equally biodiverse accompanying fauna. This increase of the Pacific
oyster correlates strongly with the occurrence of higher than average water temperatures
during July-August in these years, causing a increased success of settlement of spat (Nehls.
2007-in prep).
For the macrofauna off the Eastfrisian island of Norderney Kröncke et al. (1998) found that
abundance, species number and biomass in the 2nd quarter of the year are correlated with
SST. The SST is the mediator between the benthos and the NAO in late winter and early
spring. The results indicate that macrofaunal communities were severely affected by cold
winters, whereas storms and hot summers have no impact to the communities. It appears that
mild meteorological conditions, probably acting in conjunction with eutrophication, resulted
in an increase especially in total biomass since 1989.
On a North Sea wide scale some shifts in the distribution patterns of species have been
described (CRR NSBP Sections 5.2 and 5.3). In the German Bight examples are shifts in the
distribution of the brittle star Amphiura brachiata and the bivalve Nucula nucleus, as well as
shifts in community boundaries especially the mud-inhabiting Nucula nitidosa community.
These shifts can be understood as consequences of warming and changes in circulation and
eutrophication patterns (e.g. Rehm and Rachor, 2007). A general increase of warm-temperate
species in the southern North Sea is evident, e.g. the amphipod Megaluropus agilis and
Amphiura brachiata on the Dogger Bank, whereas cold-temperate species decreased in
abundance such as the polychaete Ophelia borealis (Wieking and Kröncke, 2001).
Shift in the climate of the North Sea towards more oceanic conditions is regarded an important
factor explaining long-term trends and drastic changes in the macrofauna of hard-bottom areas
around Helgoland (Franke and Gutow, 2004). Many of the recent records of new warmtemperate species of southern origin are indicating a continued warming since the 1980s.
In this way, Alcock (2003) studied the distribution of many benthic species, including
macroalgae, molluscs and arthropods, along the Bay of Biscay, between the end of 19th
century and 2000–2001. He determined some shifts northwards and southwards, depending on
the warm and cool periods, during the 20th century. Taking into account this development and
the IPCC scenarios of temperature increase for next 50 years, Alcock (2003) modelled the
future shift of some benthic species in the Bay of Biscay, North Sea, and Norwegian Sea.
These scenarios can be useful, for future monitoring programmes, in order to check the
northwards migration of benthic species, due to climate change.
Looking beyond the OSPAR regions, Oviatt (2004) also described a variety of temperaturemediated changes in coastal biota of NW Atlantic waters associated with the occurrence of
persistently positive values of the NAO Index in the 1980s and 1990s.
Indicative species
In the above sections, there are no presentations of data explicitly showing that observed
changes can be directly related to changes in hydrodynamics. The examples presented for the
Dogger Bank and coast off East England relate to indirect effects, mediated through larval
supply, food availability ad sediment composition.
With reference to the benthos species and habitats in the 2004 Initial List of Threatened and/or
Declining Species and Habitats the following remarks ca be made:
•
Arctica islandica – This is a northern-temperate species. A further decrease of
this species is to be expected in the North Sea as the trend of increasing sea
temperature continues;
•
Ostrea edulis – There are no clear indications that the poor status of this bivalve
species is caused by changes in temperature;
36 |
ICES BEWG Report 2007
•
Nucella lapillus – The condition of populations of this gastropod are influenced
by certain polluting substances rather than by hydrodynamics or temperature
(however, in the Basque coast, the species has disappear since 1982, due to
increasing temperatures);
•
Modiolus modiolus beds – These habitats represent a poor status since long. No
causal relationships with changes in hydrodynamics or temperature are known,
•
Intertidal Mytilus edulis beds – Data from the Wadden Sea show that part of he
beds may be taken over by the invasive Pacific oyster Crassostrea gigas. On the
other hand, however, beds of the Pacific oyster also provide adequate substrate
for settlement of new Mytilus edulis (Nehls. 2007in prep);
•
Sea-pen and burrowing fauna communities – as sea-pens are cold-temperate
species, a future decrease of his species and accompanying change in this
community can be foreseen.
Assessment and conclusions
The original question concerning the effects of changing hydrodynamics and sea temperature
on benthic communities cannot be answered without difficulties. Observations on a smaller
scale may give contradicting results. This may be caused by interference by other forcing
factors of local importance. On a large scale, changes in hydrodynamics and sea temperature
are often interconnected and are a result of climatic variability as indicated by the NAO index.
With regard to changes of hydrodynamics there is only little information available. On the
Dogger Bank increased current velocities caused changes in sediment composition and as a
consequence also in the benthic community. Off the English east coast hydrographic changes
were considered responsible for changes in food availability (derived from phytoplankton) to
the benthic community.
With regard to changes in sea temperature the following can be said: changes in the
characteristics of winters and summers play an important role in structuring the benthos.
If the trend of milder winters and warmer summers, also expressed by the NAO index,
continues, shifts in species composition and numbers, abundance and biomass can be
expected, as it is being recorded now for some of them.
No species can be named as being specifically for changes in hydrodynamic conditions,
whereas a temperature increase is indicated by shifts in the distribution of a range of several
species, e.g Megaluropus agilis and Amphiura brachiata in OSPAR region II, e.g. in OSPAR
region IV and species region II.
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årsagammenhænge og udvikling, 248 pp.
Alcock, R. 2003. The effects of climate change on rocky shore communities in the Bay of
Biscay, 1895–2050, University of Southampton, 286 pp.
Beukema, J. J. 1979. Biomass and species richness of the macrobenthic animals livng on a
tidal flat area in the Dutch Wadden Sea: effects of a severe Winter. Netherlands Journal
of Sea Research, 13: 203–223.
Beukema, J. J. 1990. Expected effects of changes in winter temperatures on benthic animals
living in soft sediments in coastal North Sea areas. In Expected effects of climatic change
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on marine coastal ecosystems, 83–92 pp. Ed. by J. J. Beukema. Kluwer Academic
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Beukema, J. J. 1992. Expected changes in the Wadden Sea benthos in a warmer world: lessons
from periods with mild winters. Netherlands Journal of Sea Research, 30: 73–79.
Bhaud, M., Cha, J. H., Duchene, J. C., and Nozais, C. 1995. Influence of temperature on the
marine fauna - what can be expected from a climatic-change. Journal of Thermal Biology,
20: 91–104.
Borja, A., Muxika, I., and Franco, J. 2006. Long-term recovery of soft-bottom benthos
following urban and industrial sewage treatment in the Nervión estuary (southern Bay of
Biscay). Marine Ecology Progress Series, 313: 43–55.
Borja, A., Franco, J., Valencia, V., Bald, J., Muxika, I., Belzunce, M. J., and Solaun, O. 2004.
Implementation of the European Water Framework Directive from the Basque Country
(northern Spain): a methodological approach. Marine Pollution Bulletin, 48: 209–218.
Buchanan, J. B., Sheader, M., and Kingston, P. F. 1978. Sources of varibility in the benthic
macrofauna off the south Northumberland coast, 1971–1976. Journal of the Marine
Biological Association of the United Kingdom, 58: 191–209.
Cook, B. I., Smith, T. M., and Mann, M. E. 2005. The North Atlantic Oscillation and regional
phenology prediction over Europe. Global Change Biology, 11: 919–926.
Craeymeersch, J. A., and Perdon, J. 2004. De halfgeknotte strandschelp, Spisula subtruncata,
in de Nederlandse kustwateren in 2003, Nederlands Instituut voor Visserijonderzoek,
IJmuiden, 12 pp.
Craeymeersch, J. A., and van Stralen, M. R. 2004. Het mosselbestand in de Westelijke
Waddenzee in het voorjaar van 2004, Nederlands Instituut voor Visserijonderzoek,
IJmuiden, 17 pp.
Daan, R., and Mulder, M. 1995. Long-term effects of OBM cutting discharges in the
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Daan, R., and Mulder, M. 2001. The macrobenthic fauna in the Dutch sector of the North Sea
in 2000 and a comparison with previous data, Neederlands Instituut foor Onderzoek der
Zee, NIOZ-Rapport 2001-2, Den Burg, Texel, 93 pp.
Dekker, R., and de Bruin, W. 2001. Het macrozoöbenthos op twaalf raaien in de Waddenzee
en de Eems-Dollard in 2000, Nederlands Instituut voor Onderzoek der Zee, Den Helder,
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Dippner, J., W., and Kröncke, I. 2003. Forecast of climate-induced change in
macrozoobenthos in the southern North Sea in spring. Climate Research, 25: 179–182.
Drinkwater, K. F., Belgrano, A., Borja, A., Conversi, A., Edwards, M., Greene, C. H.,
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climate variability associated with the North Atlantic Oscillation. Geophysical
Monograph, 134.
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Ehrich, S., and Stransky, C. 2001. Spatial and temporal changes in the southern species
component of North Sea fish assemblages. Senckenbergiana maritima, 31: 143–150.
Ehrich, S., Adlerstein, S., Brockmann, U., Floeter, J., Garthe, S., Hinz, H., Kröncke, I.,
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Franke, H.-D., and Gutow, L. 2004. Long-term changes in the macrozoobenthos around the
rocky island of Helgoland (German Bight, North Sea). Helgoland Marine Research, 58:
303–310.
Frid, C.L.J., Buchanan, J.B., and Garwood, P.R. 1996. Variability and stability in benthos:
twenty-two years of monitoring off Northumberland. ICES Journal of Marine Science,
53: 978–980.
Fromentin, J.M., and Ibanez, F. 1994. Year-to-year changes in meteorological features of the
French coast area during the last half-century - examples of 2 biological responses.
Oceanologica Acta, 17: 285–296.
Gröger, J., and Rumohr, H. 2006. Modelling and forecasting long-term dynamics of Western
Baltic macrobenthic fauna in relation to climate signals and environmental change.
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Hagberg, J., Tunberg, B.G., Wieking, G., Kröncke, I., and Belgrano, A. 2004. Effects of
climate variability on benthic communities. In Marine ecosystems and climate variation,
115–121 pp. Ed. by N. C. Stenseth, G. Ottersen, J. W. Hurrell, and A. Belgrano. Oxford
University Press, Oxford.
Hallett, T. B., Coulson, T., Pilkington, J. G., Clutton-Brock, T. H., Pemberton, J. M., and
Grenfell, B. T. 2004. Why large-scale climate indices seem to predict ecological
processes better than local weather. Nature, 430: 71–75.
Hänninen, J., Vuorinen, I., and Hjelt, P. 2000. Climatic factors in the Atlantic control the
oceanographic and ecological changes in the Baltic Sea. Limnology and Oceanography,
45: 703–710.
Holtmann, S. E., and Groenewold, A. 1994. Distribution of the zoobenthos on the Dutch
continental shelf: the western Frisian Front, Brown Bank and Broad Fourteens
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Burg, Texel, 136 pp.
Kröncke, I., and Rachor, E. 1992. Macrofauna investigations along a transect from the inner
German Bight towards the Dogger Bank. Marine Ecology Progress Series, 91: 269–276.
Kröncke, I., Zeiss, B., and Rensing, C. 2001. Long-term variability in macrofauna species
composition off the island of Norderney (East Frisia, Germany) in relation to changes in
climatic and environmental condition. Senckenbergiana maritima, 31: 65–82.
Kröncke, I., Dippner, J. W., Heyen, H., and Zeiss, B. 1998. Long-term changes in
macrofaunal communities off Norderney (East Frisia, Germany) in relation to climate
variability. Marine Ecology Progress Series, 167: 25–36.
Laine, A. O., Sandler, H., Andersin, A. B., and Stigzelius, J. 1997. Long-term changes of
macrozoobenthos in the Eastern Gotland Basin and the Gulf of Finland (Baltic Sea) in
relation to the hydrographical regime. Journal of Sea Research, 38: 135–159.
López-Jamar, E., Francesch, O., Dorrío, A. V., and Parra, S. 1995. Long-term variation of the
infaunal benthos of La Coruña Bay (NW Spain): results from a 12-year study (19821993). Scientia Marina, 59 49–61.
Oviatt, C.A. 2004. The changing ecology of temperate coastal waters during a warming trend.
Estuaries, 27: 895–904.
Planque, B., and Taylor, A. H. 1998. Long-term changes in zooplankton and the climate of the
North Atlantic. ICES Journal of Marine Science, 55: 644–654.
Rachor, E., and Nehmer, P. 2003. Erfassung und Bewertung ökologisch wertvoller
Lebensräume in der Nordsee, Bundesamt für Naturschutz, 175 pp.
Rees, H. L., Boyd, S. E., Schratzberger, M., and Murray, L. A. 2003. Benthic indicators of
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Rees, H. L., Pendle, M. A., Limpenny, D. S., Mason, C. E., Boyd, S. E., Birchenough, S., and
Vivian, C. M. G. 2006. Benthic responses to organic enrichment and climatic events in
the western North Sea. Journal of the Marine Biological Association of the United
Kingdom, 86: 1–18.
Rees, H. L., Cochrane, S., Craeymeersch, J., de Kluijver, M., Degraer, S., Desroy, N.,
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Rehm, P., and Rachor, E. 2007. Benthic macrofauna communities of the submersed
Pleistocene Elbe valley in the southern North Sea. Helgoland Marine Research, in press.
Reid, P. C., and Edwards, M. 2001. Long-term changes in the fishery, pelagos and benthos of
the North Sea. Senckenbergiana maritima, 31: 107–115.
Reid, P. C., Edwards, M., Beaugrand, G., Skogen, M., and Stevens, D. 2003. Periodic changes
in the zooplankton of the North Sea during the twentieth century linked to oceanic inflow.
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Ziegelmeier, E. 1970. Über das Massenvorkommen verschiedener makrobenthaler
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Annex 8: L o n g - t e r m s e r ie s i n T h e N e t h e r l a n d s
By J. Craeymeersch
Since 1995, 800–1,000 stations in the coastal area (up to 12km offshore) have been sampled
annually in Spring by Wageningen IMARES following a systematic sampling design.
Sampling equipment dredges over 150 m to a sediment depth of 7 cm and a width of 10 cm,
i.e. the sample surface is 15–30 m2, and the mesh width is 5 mm. In the coastal area in the SW
of the Netherlands, monitoring started in 1993. The surveys provide information on spatiotemporal variations in density, biomass and stocks of commercial species, but also result in a
time-series of abundance and biomass data of another 25 infaunal and epifaunal species.
Yearly reports (in Dutch) are made on the standing stock, spatial distribution and temporal
variation of cockles (Cerastoderma edule), through shells (Spisula subtruncata) and, recently,
razor shells (Ensis sp.) although the stocks of the latter are largely underestimated. Different
species show different patterns (Figure A8.1). The same hold for other species, as shown by
Craeymeersch & Wijsman (2006) in a study on the spatial and temporal variation of selected
bivalves in the Voordelta (SW Netherlands) (Figure A8.2).
Wijnhoven et al (2006) analysed patterns in total densities, biomasses and diversity (Shannon)
in the Voordelta for the period 1983–2004, based on box-corer and van Veen samples (1mm
mesh sieve). The data originate from different programmes that many times only covered part
the area and used different sampling designs. This, consequently, hampered thorough
statistical analyses. The data show, however, that both density and biomass significantly
increased. In most subareas, there appeared to be a trend-reversal pattern: a decrease followed
by an increase. Minimum values were observed in the period 1995–1997. Diversity did not
change significantly, but subareas showed opposite trends: and increase in the northern part of
the study area, and decrease in the south.
Craeymeersch and Rietveld (2005) report on the changing distribution of dog whelks
(Nassarius sp.). In the period 1995–2000 only a single specimen was found, near the harbour
of Rotterdam. Since then the number of observations of dog whelk has increased, and the
species is extending its distribution northwards (Figure A8.3). Craeymeersch & Perdon (2005)
report on the recent appearance of otter shells (Lutraria sp.) in the Dutch coastal waters
(Figure A8.4). These two examples most likely point to responses to climatic changes.
Analogous monitoring designs as mentioned above are used by Wageningen IMARES in other
Dutch marine waters (Wadden Sea, Westerschelde, Oosterschelde), enabling the making a
distinction between regional vs. (more) global patterns. A good example is the trend of the
Baltic tellin (Macoma balthica) in the Dutch waters (Figure A8.5). In the western part of the
Wadden Sea a decline in the stock over the last five years has been observed, in contrast to the
whole Wadden Sea (although the stock in 2005 was the lowest measured) and other water
bodies. The decrease in the western Wadden Sea has been reported before and been ascribed
to climate-related changes in the recruitment (Philippart et al 2003). But, apparently, the
decrease in the western Wadden Sea is a more regional phenomenon (Craeymeersch and
Perdon 2005).
References
Craeymeersch, J. A., and Perdon, J. 2004. De halfgeknotte strandschelp, Spisula subtruncata,
inde Nederlandse kustwateren in 2004. RIVO Rapport, C073/04. RIVO: Yerseke, The
Netherlands. 27 pp.
Craeymeersch, J., and Perdon, J. 2005. De otterschelp Lutraria in de Nederlandse wateren.
Het Zeepaard 65(5): 144–150.
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Craeymeersch, J., and Rietveld, M. 2005. Dog whelks in Dutch coastal waters. MarBEF
Newsletter, 3: 22–24.
Craeymeersch, J. A., and Perdon, J. 2006. De halfgeknotte strandschelp, Spisula subtruncata,
in de Nederlandse kustwateren in 2005. RIVO Rapport, C036/06. RIVO: Yerseke, The
Netherlands. 22 pp.
Craeymeersch, J. A. and Wijsman, J. W. M. 2006. Ruimtelijke verschillen en temporele
fluctuaties in het voorkomen van een aantal schelpdieren in de Voordelta. Wageningen
IMARES Report, C013/06. Wageningen IMARES: IJmuiden, The Netherlands. 29 pp.
Philippart, C. J. M., van Aken, H., Beukema, J., Bos, O., Cadée, G. C., and Dekker, R 2003.
Climate-related changes in recruitment of the bivalve Macoma balthica. Limnology and
Oceanography, 48: 2171–2185.
Spisula subtruncata
700
stock (milj kg)
600
500
400
300
200
100
0
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2001
2002
2003
2004
2005
year
Ensis sp.
70000
stock (milj individuals)
60000
50000
40000
30000
20000
10000
0
1995
1996
1997
1998
1999
2000
year
Figure A8.1. Temporal fluctuation of stock of through shells, Spisula subtruncata (milj kg
freshweight) and razor shells, Ensis sp. (milj individuals) in the Dutch coastal area (Craeymeersch
& Perdon 2004; Perdon ….. 2006).
ICES BEWG Report 2007
C er ast o d er ma ed ul e
ind/m2
30
1.0
0.8
0.6
0.4
0.2
0.0
20
0
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
0.8
ind/m2
Te l l i na f a bul a
D ona x v i t t a t us
0.6
0.4
0.2
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1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
0.0
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
ind/m2
0.8
0.6
0.4
0.2
0.0
Ensis sp .
10
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
ind/m2
42 |
ind/m2
80
60
Sp i sula sub t r uncat a
40
20
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
0
Figure A8.2. Temporal variation of the density (ind/m2) of selected bivalves in the Voordelta (SW
Netherlands) (Craeymeersch and Wijsman 2006).
Figure A8.3 Distribution records for Nassarius observed between 1995 and 2004 in the Dutch
coastal waters (Craeymeersch and Rietveld 2005).
ICES BEWG Report 2007
| 43
Figure A8.4. Distribution records for Lutraria observed between 1995 and 2004 in the Dutch
coastal waters (no records before 2002) (Craeymeersch and Perdon, 2005)
2005
2004
2003
2002
2001
2000
1999
1998
1997
1996
1995
stock (milj ind)
2500
2000
1500
1000
500
0
stock (milj ind)
4000
2000
stock (milj ind)
6000
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2005
2004
2003
2002
2001
2000
1999
1998
1997
1996
1995
1994
1993
1992
stock (milj ind)
Westerschelde
8000
0
Oosterschelde
balthica) in Dutch waters (Craeymeersch and Perdon, 2006)
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
stock (milj ind)
44 |
ICES BEWG Report 2007
Wadden Sea
100000
80000
60000
40000
20000
0
w estern Wadden Sea
40000
30000
20000
10000
0
Dutch coastal area
25000
20000
15000
10000
5000
0
Figure A8.5. Temporal fluctuations in the stock (milj individuals) of the Baltic telllin (Macoma
ICES BEWG Report 2007
| 45
Annex 9: Cu rre nt act i vit ies o f t he b ent h os g ro up o f I PI MA R
By Miriam Tuaty Guerra and Marria José Gaudêncio
WATER FRAME DIRECTIVE
Benthic macroinvertebrates are currently monitored since February 2006 at several locations
along the Portuguese coast (Figure A9.1). Basic structural parameters, species richness,
abundance and biomass, together with sediment grain size and organic matter are under study.
So far 4 sampling surveys took place: February and July 2006 (coastal waters and emissaries),
March and September 2006 (estuaries).
Data are still at an early stage of processing. So far very preliminary results may be provided
(Tables A9.1–A9.4) as well as a first approach to the ecological quality status of the estuaries
under study based on the M-AMBI index (Table A9.5).
46 |
ICES BEWG Report 2007
Table A9.1. List of the taxa present at the coastal waters sampling sites (see Figure A9.1 for
locations).
ANNELIDA
POLYCHAETA
Aonides paucibranchiata (Southern, 1914)
Diopatra neapolitana (Delle Chiaje, 1841)
Eumida sanguinea (Oersted, 1843)
Glycera lapidum (Quatrefages, 1865)
Glycera tridactyla (Schmarda, 1861)
Goniada emerita (Oersted, 1843; Audouin and Milne-Edwards, 1843)
Lanice conchilega (Pallas, 1766)
Magelona filiformis (Wilson, 1959)
Magelona johnstoni (Fiege, Licher and Mackie, 2000)
Malacoceros ciliatus (Keferstein, 1862)
Mediomastus capensis (Day, 1961)
Nephtys assimilis (Oersted, 1843)
Nephtys cirrosa (Ehlers, 1868)
Nephtys hombergii (Savigny, 1818)
Notomastus latericeus (M. Sars, 1851)
Owenia fusiformis (Delle Chiaje, 1842)
Pherusa monilifera (Delle Chiaje, 1841)
Phyllodoce (Anaitides) maculata (Linné, 1767)
Phyllodoce laminosa (Savigny, 1818)
Prionospio caspersi (Laubier, 1962)
Scolelepis?gilchristi (Day, 1961)
Scoletoma impatiens (Claparède, 1868)
Sigalion mathildae (Audouin and Milne-Edwards in Cuvier, 1830)
Spio decoratus (Bobretzky, 1870)
Spiophanes bombyx (Claparède, 1870)
ARTHROPODA CRUSTACEA
AMPHIPODA
Abludomelita obtusata (Montagu, 1813)
Ampelisca brevicornis (Costa, 1853)
Ampelisca diadema (Costa, 1853)
Ampelisca rubella (A. Costa, 1864)
Ampelisca spooneri (Dauvin and Bellan-Santini, 1982)
Atylus falcatus (Metzger, 1871)
Bathyporeia pelagica (Bate, 1856)
Hippomedon denticulatus (Bate, 1857)
Idunella longirostris (Chevreux, 1820)
Megaluropus agilis (Hoeck, 1889)
Orchomenella nana (Kroyer, 1846)
Pontocrates altamarinus (Bate and Westwood, 1862)
Urothoe pulchella (Costa, 1853)
CUMACEA
Diastylis bradyi Norman, 1879
Iphinoe trispinosa (Goodsir, 1843)
ICES BEWG Report 2007
DECAPODA
Diogenes pugilator (Roux, 1829)
Liocarcinus vernalis (Risso, 1816)
Polybius henslowii (Leach, 1820)
Processa sp.
Thia scutellata (Fabricius 1793)
ISOPODA
Eurydice truncata (Norman, 1868)
MYSIDA
Gastrosaccus spinifer (Goës, 1864)
ECHINODERMATA
SPATANGOIDA
Echinocardium cordatum (Pennant, 1777)
OPHIURIDA
Amphiura (Acrocnida)brachiata (Montagu, 1804)
Ophiura grubei (Heller, 1863)
MOLLUSCA
BIVALVIA
Abra alba (Wood W., 1802)
Donax vittatus (Da Costa, 1778)
Ensis?arcuatus (Jeffreys, 1865)
Mactra stultorum (Linné, 1758)
Montacuta ferruginosa (Montagu, 1808)
Mysella bidentata (Montagu, 1803)
Pharus legumen (Linné, 1758)
Phaxas pellucidus (Pennant, 1777)
Spisula solida (Linné, 1758)
Spisula subtruncata (Da Costa, 1778)
Tellina fabula (Gmelin, 1791)
Tellina (Moerella) pygmaea (Linné, 1758)
Thracia papyracea (Poli, 1791)
Venus casina (Linné, 1758)
GASTROPODA
Euspira catena (da Costa, 1778)
Nassarius reticulatus (Linné, 1758)
NEMATODA
NEMERTINA
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ICES BEWG Report 2007
Table A9.2 List of the taxa present at the sampling stations located in the vicinity of urban and
industrial emissaries (see Figure A9.1 for locations).
ANNELIDA
POLYCHAETA
Diopatra neapolitana (Delle Chiaje, 1841)
Diplocirrus glaucus (Malmgren, 1867)
Flabelligeridae não identificados
Glycera gigantea (Quatrefages, 1865)
Glycera lapidum (Quatrefages, 1865)
Glycera tridactyla (Schmarda, 1861)
Goniada maculata (Oersted, 1843)
Gyptis capensis (Day, 1963)
Hesionidae (fragments)
Lumbrineridae (fragments)
Magelona filiformis (Wilson, 1959)
Magelona johnstoni (Fiege, Licher and Mackie, 2000)
Maldanidae (fragments)
Mediomastus capensis (Day, 1961)
Nephtys assimilis (Oersted, 1843)
Nephtys cirrosa (Ehlers, 1868)
Nephtys hombergii (Savigny, 1818)
Notomastus latericeus (M. Sars, 1851)
Ophelia neglecta (Schneider, 1887)
Orbinia latreilli (Audouin and Milne-Edwards, 1833)
Owenia fusiformis (Delle Chiaje, 1842)
Pherusa monilifera (Delle Chiaje, 1841)
Pherusa sp.
Phyllodoce (Anaitides) maculata (Linné, 1767)
Phyllodoce laminosa (Savigny, 1818)
Phyllodocidae (fragments)
Prionospio cirrifera (Wirén, 1883)
Protodorvillea kefersteini (McIntosh, 1869)
Scolelepis bonnieri (Mesnil, 1896)
Scolelepis squamata (O. F. Müller, 1789)
Scolelepis tridentata (Southern, 1914)
Sigalion mathildae (Audouin and Milne Edwards in Cuvier, 1830)
Spio decoratus (Bobretzky, 1870)
Spionidae (fragments)
Spiophanes bombyx (Claparède, 1870)
Sthenelais limicola (Ehlers, 1864)
ARTHROPODA CRUSTACEA
AMPHIPODA
Ampelisca brevicornis (Costa, 1853)
Ampelisca diadema (Costa, 1853)
Ampelisca spinipes Boeck, 1861
Ampelisca spooneri (Dauvin and Bellan-Santini, 1982)
Ampelisca tenuicornis (Liljeborg, 1855)
ICES BEWG Report 2007
Atylus falcatus (Metzger, 1871)
Bathyporeia pelagica (Bate, 1856)
Hippomedon denticulatus (Bate, 1857)
Orchomenella nana (Kroyer, 1846)
Pontocrates altamarinus (Bate andWestwood, 1862)
Tryphosites longipes (Bate and Westwood, 1861)
Urothoe poseidonis (Reibish, 1905)
CUMACEA
Cumopsis longipes (Dohrn, 1869)
Diastylis bradyi (Norman, 1879)
Eocuma dolfusi (Calman, 1907)
Iphinoe trispinosa (Goodsir, 1843)
DECAPODA
Diogenes pugilator (Roux, 1829)
Liocarcinus vernalis (Risso, 1816)
Pagurus bernhardus (Linné, 1758)
Polybius henslowii (Leach, 1820)
ISOPODA
Eurydice spinigera (Hansen, 1890)
MYSIDACEA
Gastrosaccus spinifer (Goës, 1864)
ECHINODERMATA
ECHINOIDEA
Echinocardium cordatum (Pennant, 1777)
Spatangoida (fragments)
OPHIUROIDEA
Amphiura (Acrocnida)?brachiata (Montagu, 1804)
Amphiura chiajei (Forbes, 1843)
Amphiura (Acrocnida)?semisquamata (Koehler, 1914)
Amphiura ?filiformis (O. F. Müller, 1776)
Amphiura sp.
Ophiura albida (Forbes, 1839)
Ophiuroidea (fragments)
MOLLUSCA
BIVALVIA
Abra alba (Wood, 1802)
Clausinella fasciata (Da Costa, 1778)
Donax vittatus (Da Costa, 1778)
Dosinia lupinus (Linné, 1758)
Goodalia triangularis (Montagu, 1803)
Montacuta ferruginosa (Montagu, 1808)
Mysella bidentata (Montagu, 1803)
Pharus legumen (Linné, 1758)
Phaxas pellucidus (Pennant, 1777)
Solenidae (fragments)
Spisula solida (Linné, 1758)
Spisula subtruncata (Da Costa, 1778)
Tellina fabula Gmelin, 1791
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ICES BEWG Report 2007
Tellina (Moerella) donacina Linné, 1758
Tellina (Moerella) pygmaea Lovén, 1846
Thracia ?papyracea (Poli, 1791)
Venerupis pullastra (Montagu, 1803)
Venus casina Linné, 1758
GASTROPODA
Cylichna cylindracea (Pennant, 1777)
Euspira guillemini (Payraudeau, 1826)
Nassarius reticulatus (Linné, 1758)
NEMATODA
NEMERTINA
ICES BEWG Report 2007
| 51
Table A9.3. Taxa present at the sampling stations located in the river Minho estuary (mean
numbers/0.1 m2), in September 2007. Stations are cited from downstream (station 1) to
downstream (Station 4). Station 5 is intertidal located in the vicinity of the river mouth.
TAXA
SAMPLING STATIONS
1
2
3
4
5
0
3
2
0
ANNELIDA
OLIGOCHAETA
POLYCHAETA
Chaetozone gibber (Woodham and Chambers, 1994)
-
0
0
0
0
Nephtys assimilis (Oersted, 1843)
-
0
0
0
0
Nephtys cirrosa (Ehlers, 1868)
-
0
0
0
0
Nephtys hombergii (Savigny, 1818)
-
0
0
0
0
Nereis (Hediste) diversicolor (O.F. Müller, 1776)
-
0.3
0.3
0
0
Pectinaria (Lagis) koreni (Malmgren, 1866)
-
0
0
0
0
Pisione remota (Southern, 1914)
-
0
0
0
0
Scolaricia typica (Eisig, 1914)
-
0
0
0
0
ARTHROPODA CRUSTACEA
0
AMPHIPODA
0
Ampelisca brevicornis (Costa, 1853)
-
0
0
0
0
Ampelisca diadema
-
0
0
0
0
Corophium multisetosum (Stock, 1952)
-
0
0
0
430
-
0
0
0
1
Abra alba (Wood W., 1802)
-
0
0
0
0
Nucula nitidosa (Winckworth, 1930)
-
0
0
0
0
Spisula subtruncata (da Costa, 1778)
-
0
0
0
0
-
0
0
0
0
DECAPODA
Crangon crangon (Linné, 1758)
MOLLUSCA
BIVALVIA
GASTROPODA
Nassarius reticulatus (Linné, 1758)
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ICES BEWG Report 2007
Table A9.4. Taxa present at the sampling stations located in the river Lima estuary (mean
numbers/0.1 m2), in September 2007. Stations are cited from downstream (station 1) to
downstream (station 4).
TAXA
SAMPLING STATIONS
1
2
3
4
0
2
0
1
Chaetozone gibber (Woodham and chambers,
1994)
0.3
0
0
0
Nephtys assimilis (Oersted, 1843)
0.3
0
0
0
Nephtys cirrosa (Ehlers, 1868)
0
0.3
0
0
Nephtys hombergii (Savigny, 1818)
1
0
0
0
Nereis (Hediste) diversicolor(O.F. Müller, 1776)
0
0
0
0
Pectinaria (Lagis) koreni (Malmgren, 1866)
1
0
0
0
Pisione remota (Southern, 1914)
0
2
0.3
0.3
Scolaricia typica (Eisig, 1914)
0
1
0
0
ANNELIDA
OLIGOCHAETA
POLYCHAETA
ARTHROPODA CRUSTACEA
AMPHIPODA
Ampelisca brevicornis (Costa, 1853)
0.3
0
0
0
Ampelisca diadema
0.3
0
0
0
Corophium multisetosum (Stock, 1952)
0
0
10
0
0
0
0
0
DECAPODA
Crangon crangon (Linné, 1758)
MOLLUSCA
BIVALVIA
Abra alba (Wood, 1802)
8
0
0
0
Nucula nitidosa (Winckworth, 1930)
2
0
0
0
Spisula subtruncata (da Costa, 1778)
0.3
0
0
0
1
0
0
0
GASTROPODA
Nassarius reticulatus (Linné, 1758)
Table A9.5. Minho and Lima estuaries (September, 2007): Diversity indexes and ecological quality
status based on AMBI indexes.
SAMPLING STATION
H'
(LOG2)
AMBI
M-AMBI
EQS
Minho1
0,00
7,00
−0,07
Bad
Minho2
0,00
3,00
0,25
Poor
Minho3
0,33
5,70
0,17
Bad
Minho4
0,00
6,00
0,04
Bad
Minho5
0,10
2,99
0,35
Poor
Lima1
1,59
2,29
0,99
High
Lima2
1,20
2,68
0,65
Good
Lima3
0,14
2,90
0,33
Poor
Lima4
0,56
4,50
0,31
Poor
ICES BEWG Report 2007
| 53
42º
R. Minho
Porto
canyon
R. Douro
Porto
41º
PORTUGAL
é
Nazar
n
o
cany
39º
ro
R. Tejo
ca
o
Lisboa
el
.R
ch
C
i
spSetúbal
.E
C
ATLANTIC
OCEAN
Tejo
n
canyo
al
Set úb
n
o
cany
R. Sado
Sines
R. Guadiana
S.
V
ic
en
te
38º
voei
C . Car
C.
Latitude (N)
40º
37º
S.Vicente
canyon
4 000
12º
11º
10º
Faro
Portimão
canyon
3 000
9º
Longitude (W)
2 000
30
200 100
1 000
8º
7º
Figure A9.1. Portuguese mainland coast (sampling sites):
WFD: ♦estuaries; ■ coastal waters; ▲vicinity of urban and industrial emissaries.
◙ Tagus estuary: monitoring of the ecological quality.
♣ Arrábida Marine Park: monitoring of sediment and benthic macroinvertebrates within the framework of
“BIOMARES”
54 |
ICES BEWG Report 2007
Project LIFE06 NAT P 192: “BIOMARES”
Restoration and management of biodiversity in the Marine Park Site
Arrábida-Espichel (PTCON0010)
The main objective of this EU funded project is the restoration of the seagrass meadow in the
Portinho da Arrábida (habitat 1110 - NATURA 2000) by planting 10 ha of seagrass using the
species Zostera marina and Cymodocea nodosa. Natural recovery is expected to continue to
30 ha by natural seagrass growth after the project, which will last until 2010. Seagrass recover
is expected to increase biodiversity in the area.
The task of the IPIMAR benthos group is the study of the benthic macroinvertebrates in the
transplant areas and in the adjacent areas. Both had very abundant benthos in the 1970s when
the seagrass meadow was fully developed. The first sampling survey took place in early April.
The sampled areas are shown in Figure A9.2. At the moment sediment grain size and OM are
under analysis and the fauna is being sorted.
Figure A9.2. Arrábida Marine Park: planting areas of Zostera marina and Cymodocea nodosa
(dark-red). Adjacent area (dark-blue).
Ecological quality status of the Tagus estuary
Contract with SIMTEJO (Management and treatment of residual waters of the
rivers Tagus and Trancão - city of Lisbon)
Since 2004 several physical and chemical parameters and benthic macroinvertebrates have
been monitored in order to assess the ecological quality status of the estuary and to provide
advice for a sustainable management.
The results of the 2004 surveys (Figure A9.3), suggest a moderate ecological quality, in global
terms. Fauna-environment relations are rather puzzling; the main factor structuring the fauna
appears to salinity. Nevertheless, in a few sites with high input of contaminants the
macrozoobenthos seem to reflect those inputs (see BIO-ENV results, Figure A9.3). We hope
that further results will help to clarify the issue.
ICES BEWG Report 2007
| 55
N
39º
M-AMBI: 2004
V. F. Xira
38.95º
38.9º
38.85º
Ecological Quality
Good (12)
Moderate (6)
Poor (16)
Bad (6)
Sacavém
38.8º
LISBOA
38.75º
Oeiras
P. Comércio
38.7º
23
Cacilhas
38.65º
Barreiro
38.6º
-9.35º -9.3º -9.25º -9.2º -9.15º -9.1º -9.05º
-9º
-8.95º -8.9º
Figure A9.3 The Tagus estuary (Lisbon): Sites distribution according to M-AMBI and BIO-ENV
results.
IPIMAR, Lisboa, 23 April 2007
W
56 |
ICES BEWG Report 2007
Annex 10: Lo n g t er m c ha ng es i n t h e p h yt obe nt h ic
co mm uni t ies o f t h e Ba lti c Se a
Long term changes in the plant species depth distribution indicate a recovery of the coastal
Baltic Sea systems. Revisit of Mats Waern diving sites in the Gräsö area, Åland Sea, from
1940–1942 in 1984 indicated a drastic decrease of the depth distribution of plants as
demonstrated by the bladder wrack (Fucus vesiculosus) which on average had reduced its
depth distribution by 3 m. A revisit in 1992 indicated an increase in the depth distribution of
the plants and in 2006 Fucus was found at the same depths as in the 1940th on several of the
revisited stations, and all showed an increase in dept distribution.
Figure A10.1. The average depth distribution of Fucus vesiculosus on the Mats Waern sites, Gräsö
area, Åland Sea, comparison between the years 1942, 1984, 1996 and 2006 (from Anders Wallin et
al. in prep.).
This somewhat sensational result is to a part also verified by the plant species distribution in
the northern Baltic proper (the Askö area). In the Askö area, on average Fucus has increased
its depth distribution since the mid 1990th. This is especially clear when analyzing each
station with itself over a given time period. On several stations the Fucus communities have
increased their depth distribution since the beginning of the 1990th. However, in some places
they have disappeared most probably due to population dynamics. In some stations Fucus has
reoccurred, which also is reported from other areas and therefore seems to be a general trend
in the Baltic Sea. On a few stations Fucus has not increased the depth distribution due to the
lack of suitable substrate deeper down. Also, several other plant species, including higher
plants, are growing deeper down today compared to the early 1990th. However, the general
trend is not straight forward. Depending on population dynamics and also probably due to a
minor decrease in the salinity, some species have decreased (e.g. Rhodomela confervoides) or
have reappeared and increased their distribution (e.g. Sphacelaria arctica). In conclusion, a
recovery in the near shore coastal system of the Baltic Sea can be observed. This is also
confirmed by the increasing local Secchi depth, decrease in nitrogen load and decreased
pelagic primary production during the spring bloom.
ICES BEWG Report 2007
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ICES BEWG Report 2007
Annex 11: F i nal r ep ort o n t h e e f fe ct s of t he P r es ti ge oi l sp il l
o n c o nt i n e nt a l s he lf m a c r o i n fa u na ( Ga li c ia , N W S p a i n )
ICES Benthos Ecology Working Group
Working document, Wilhelmshaven, Germany, April 2007
Not to be cited without reference to author(s)
F i nal r ep ort o n t h e e f fe ct s of t he P r es ti ge oi l sp il l o n
co nt i ne nt a l s he lf m a c r o i nf a u n a ( Ga li ci a , N W Spa i n )
S. Parra, I. Frutos & J. Valencia
Instituto Español de Oceanografía, Centro Oceanográfico de La Coruña, Apdo. 240, 15001 La
Coruña, Spain.
INTRODUCTION
After the grounding of the tanker Prestige on November 2002 near the Galician Bank, NW
Spain, about 50000 tons of heavy oil (type M-100) was released to the sea, affecting a huge
part of the Galician coastline and surroundings areas (Sánchez 2003; Sánchez et al., 2003a).
Documents presented in 2003, 2004 and 2005 in this working group dealt with the general
information about this oil spill, as well as with its initial effects on the benthic and demersal
continental shelf communities. The paper presented in 2003 provided general information on
this oil spill, in addition to the actions carried out by the IEO towards the study of its impact
on the continental shelf of Galicia and Asturias (Sánchez et al., 2003b). The 2004 report
provided new data on the evolution of the benthic and demersal communities of the shelf
affected (Sánchez et al., 2004) and the 2005 report presented new results on the infaunal and
hyperbenthic communities of this ecosystem (Parra et al., 2005). This final report presents the
main results on macroinfaunal communities obtained after three years of sampling (20022004) in the Galician continental shelf.
MATERIAL AND METHODS
To study the sediment characteristics, sediment samples were collected from 23 stations
distributed over three impact zones (1: min; 2: max; 3: moderate) and three depth strata (A:
70–120 m; B: 121–200 m; C: 201–300 m; Figure A11.1). The sampling procedure was
repeated in these stations during five different periods: winter 2002, spring 2003, autumn
2003, spring 2004 and autumn 2004, with the exception of depth stratum C which was only
sampled in the spring of 2004. Particle size analysis was performed by a combination of dry
sieving and sedimentation techniques (Buchanan, 1984). Organic matter in the sediment was
estimated as weight loss of dried (100 ºC, 24 h) samples after combustion (500 ºC, 24 h). An
additional sample was taken to measure the Redox potential, which was performed using a
combined Redox electrode and a portable pH meter in recently extracted box corers.
Measurements were recorded at three sediment levels: 0–1, 3–4 and 6–7 cm depth.
Infaunal samples were collected with a modified Bouma box corer (0.0175 m2) and 3–5
samples were taken (sampling area = 0.0525–0.0875 m2) in each station (Figure A11.1). This
sampler has been used successfully to study the impact of the Aegean Sea oil spill on the
sublittoral infaunal communities of the rías of La Coruña, Ferrol and the near continental shelf
(López-Jamar et al., 1996).
Samples from 13 stations were collected for the study of the infaunal communities (figure 1).
It was only possible to sample the bathymetric strata A and B in zones 1 and 2. The infaunal
communities of stations 1, 2, 4 and 5 belonging to zone 1, stations 7, 8, 10, 11, 13 and 14 of
zone 2 and stations 16, 17 and 19 of zone 3 were studied. To examine the temporal evolution
ICES BEWG Report 2007
| 59
of the infaunal communities, the samplings were repeated in the same stations over the course
of five different time periods: winter 2002–2003, spring 2003, autumn 2003, spring 2004 and
autumn 2004 (with the exception of zone 1 when only two time periods were studied: winter
2002–2003 and spring 2003).
44.0°
Sector 3
43.5°
0
50
0
20
0
10
Sector 2
e
ort
M
da
sta
o
C
Espatial infauna stations
43.0°
Temporal infauna stations
Finisterre Cape
Sediment stations
s
Ría
42.5°
xas
Bai
Sector 1
50 km
10.0°
9.5°
9.0°
8.5°
8.0°
Figure A11.1 General view of sampling and bottom stations.
Macroinfauna samples were sieved on board through a 0.5 mm sieve, anaesthetized with a
MgCl2 solution and then preserved with 8 % buffered formaldehyde. Correlations of wet
weight (WW) to ash-free dry weight (AFDW) were calculated to estimate the biomass of each
individual species (López-Jamar et al., 1996; Parra & López-Jamar, 1997).
RESULTS
Distribution of tar aggregates
As a result of the Prestige Oil Spill, the oil degradation and sedimentation through the water
column caused the presence of tar aggregates on the bottom. This heavy oil appeared in
aggregates of between 1 and 20 cm in diameter. The existence of particles of less than 10 mm
could not be determined owing to the beam trawl mesh size, which means, with respect to the
results obtained, that at the very least the quantities indicated were present. The concentrations
in each of the three zones considered, expressed in kg of oil • km−2, are shown in Figure
A11.2. The highest mean concentrations of oil were found in winter in Zone 2 (off the Costa
da Morte), diminishing progressively over time until they reached very low levels (0.5 kg •
km−2) in autumn 2004, which is close to our detection limit. In Zone 1, the mean density of tar
aggregates was always very low (<0.1 kg • km−2). Therefore, this study considers it to be the
zone suffering the least impact.
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ICES BEWG Report 2007
Tar aggregates (kg · km-2)
180
160
Zone 1
Zone 2
Zone 3
140
120
100
80
60
40
20
0
Winter 02
Spring 03
Autumn 03
Spring 04
Autumn 04
Figure A11.2 Heavy oil (tar aggregates) average concentrations (kg • km−2 ± SE) on the Galician
continental shelf from five beam-trawl surveys.
Sediment characteristics
Table A11.1 presents the sediment variables in the stations surveyed. The sediment of the
shallowest stratum (stratum A) in Zone 1, the area suffering the least impact from the oil spill,
is characterized by the presence of sediment types dominated by mud (station 1) or fine sands
(station 4), with the mean diameter having temporal fluctuations within relatively close
boundaries (from 41 ± 1 to 66 ± 10 µm, at stations 1 and 4 respectively). Organic matter
content was moderate, ranging from 4.02 ± 0.43 % at station 1 to 2.98 ± 10.36 at station 4.
The selection varied from poor (station 1) to moderate (station 4). In terms of the temporal
variation of the sediment between the different periods under study, no major changes were
found. (Figure A.11.3; Table A11.1).
ICES BEWG Report 2007
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Organic matter
Mean grain size
PHI
%
6
Pontevedra transect
Pontevedra transect
6
Muros transect
Muros transect
5
1
4
4
1
4
3
2
3
4
3
5
6
5
2
2
2
6
Sector 1
Sector 1
1
0
50
100
150
200
250
300
50
100
150
200
250
300
6
Corcubión transect
Muxía transect
Laxe transect
7
4
11
Laxe transect
4
9
14
13
3
Corcubión transect
7
6
Muxía transect
5
12
15
13
8
9
8
2
15
10
11
10
12
14
2
Sector 2
Sector 2
1
0
50
100
150
200
250
300
50
100
150
200
250
300
6
Caión transect
Caión transect
Coruña transect
5
6
Coruña transect
Cedeira transect
Cedeira transect
17
4
16
21
17
18
16
4
23
20
3
19
21
20
22
18
2
22
2
23
19
Sector 3
Sector 3
1
0
50
100
150
200
Water depth (m)
250
300
50
100
150
200
250
300
Water depth (m)
Figure A11.3. Effect of water depth at stations on mean diameter of particle size (Φ Units) and
percentage of organic matter in sediments on the continental shelf off Galicia by zones (zones).
The middle stratum (stratum B) of Zone 1, the zone suffering the least impact, is characterized
by the presence of sediments made up of fine sands (between 167 ± 4 and 165 ± 9 µm, stations
2 and 5 respectively), with a moderate organic content (between 3.60 ± 0.21 and 2.40 ± 0.56
%, stations 2 and 5 respectively; Figure A11.3). The selection of the two stations is fairly
good, without exceeding the sorting coefficient of 1.31 ± 0.02 points at station 5 (Figure
A11.3; Table A11.1). The temporal variation did not exhibit any major changes, either.
The sediments of the stations located in the deepest stratum (stratum C) in Zone 1, which were
only sampled during the spring, 2004 survey, were composed of sediment types that fluctuated
between the very fine sands of station 3 and the fine sands of station 6, with diameters ranging
from 85 and 158 µm respectively. Station 6 presents a very low organic content (1.92 %)
which varies up to moderate in station 3 (3.00 %). Sediment selection went from moderately
good to moderate (S0 between 1.30 and 1.33, stations 6 and 3 respectively; Figure A11.3,
Table A11.1).
Nine stations from the maximum-impacted area (Zone 2) were sampled –three in the
shallowest stratum (Stratum A; stations 7, 10 and 13), three in the middle (Stratum B; stations
8, 11 and 14) and three from the deep stratum (Stratum C; stations 9, 12 and 15), the latter
having only been sampled in the spring, 2004 survey. The bottoms of the shallowest stratum
(stratum A) in this zone present all of the sediment types, ranging from mud sediment at
station 7 (Q50 = 41 ± 6 µm) to fine sands with low organic matter content at station 10 (Q50 =
161 ± 11 µm). Station 13 exhibited moderate organic content (3.32 ± 0.26 %) which varied up
to the highest value found in the study at station 7 (6.35 ± 0.14 %). Sediment selection ranged
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between poor (station 7) and moderate (stations 11 and 13; Figure A11.3, Table A11.1). The
temporal variation of the sediment in the stations belonging to this stratum, for Zone 2, was
minor.
The middle stratum of Zone 2, was also characterized by the presence of sandy sediments,
made up of very fine sands, with a mean particle diameter ranging from 79 ± 4 µm at station
11 and 120 ± 17 µm at station 8. In terms of organic content, the values fluctuated between
2.24 ± 0.37 % at station 8 and the moderate value found at station 14 (3.15 ± 0.49 %). The
sediment selection was moderate, with values between 1.50 ± 0.02 and 165 ± 0.17
corresponding to stations 6 and 11, respectively. No substantial temporal variations were
observed in the sediment characteristics by stratum and zone (Figure A11.3; Table A11.1).
The sediments in the stations located in the deepest stratum (stratum C) of Zone 2, which was
only sampled in the spring, 2004 survey, were composed of sediment types ranging from very
fine sands at station 9 and fine sands at stations 12 and 15, with diameters from 88 to 151 µm,
for stations 9 and 15, respectively. Station 9 presented a relatively moderate organic content
(2.63 %) ranging on the scale up to moderate at stations 12 and 15 (3.24 and 3.26 %,
respectively). The sediment selection was between moderately good and poor (S0 between
1.29 and 1.99, stations 9 and 12 respectively; Figure A11.3; Table A11.1).
In the moderate-impacted zone (Zone 3) eight stations were sampled –two in the shallowest
stratum (stations 16 and 19), three in the middle (stations 17, 20 and 22) and three from the
deepest stratum (stations 18, 21 and 23), the latter having been sampled only in the spring,
2004 survey. The sediments of the shallowest stratum (stratum A) in this zone had very fine
sands at station 16 (Q50 = 86 ± 12 µm) with fine sands and low organic matter content at
station 19 (Q50 = 147 ± 13 µm). Station 19 was low in organic content (1.20 ± 0.11 %) which
fluctuated until reaching a high value for organic content at station 16 (4.18 ± 0.36 %).
Sediment selection was moderate with the sorting coefficient ranging from 1.68 ± 0.13 at
station 16 to 1.36 ± 0.06 at station 19. The temporal variation of the sediment in the stations
from this stratum in Zone 3 was minor (Figure A11.3; Table A11.1).
The middle stratum in Zone 3 was also characterized by the presence of sandy sediments, that
range from very fine sands with a mean particle diameter of between 85 ± 17 µm (station 17)
and 122 ± 21 µm (station 20) to fine sands with a mean diameter of 155 ± 18 µm (station 22).
In terms of organic content, the values ranged from 2.58 ± 0.32 % at station 22 and the
moderate value at station 17 (3.99 ± 0.34 %). Sediment selection varied between moderate and
poor, with values fluctuating between 1.37 ± 0.05 and 2.46 ± 0.25, at stations 22 and 17
respectively. On a temporal level, there were no important fluctuations in the sediment
characteristics by stratum and zone (Figure A11.3; Table A11.1).
The sediments of the stations located in the deepest stratum (stratum C) in zone 3, which were
only sampled in the spring 2004 survey, were made up of sediment types that ranged from
very fine sands at station 21 to fine sands at stations 18 and 23, with diameters of between 88
and 177 µm, at stations 21 and 23, respectively. Station 18 presented a relatively high organic
content (4.23 %) which was moderate at stations 21 and 23 (3.09 and 3.76 %, respectively).
Sediment selection ranged from moderate to poor (S0 between 1.42 and 2.19, stations 23 and
21 respectively; Figure A11.3; Table A11.1)).
General characteristics of infaunal communities
This section offers a brief description of the general faunal characteristics of the
macroinfaunal communities studied, by zone and depth stratum. All stations were sampled on
a seasonal basis, with data being provided from five surveys between the years 2002 to 2004.
The next section will focus on the temporal variation of the community in relation to the
possible effects of the oil spill.
ICES BEWG Report 2007
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In the 71–120 m depth stratum (stratum A) in Zone 1, the minimum-impacted area, we
analyzed a total of two stations (1 and 4) characterized by a mud sediment (station 1) or
having very fine sands (station 4) with a moderate organic content (Figure A11.3; Table
A11.1). The two stations were sampled in the surveys carried out only in winter 2002, spring
2003 and 2004. Polychaetes were the dominant zoological group in abundance in this stratum
(as high as 92.31 % in spring at station 4; tables 3 and 4). The communities were dominated
by the spionid polychaete Prionospio fallax, which reached an average abundance of 2079 ind
• m−2 in station 4 (table 5). In the 121-200 m depth stratum (stratum B) in Zone 1, the two
stations studied (2 and 5) in the same period of time as the previous stratum, presented
sediments made up of fine sands with a moderate organic content (Table A11.1), Polychaetes
were the dominant zoological group in abundance in this stratum (91.57 % in winter 2002, in
station 2), but in biomass Echinoderms were the dominant group in Stn. 10 (Tables A11.3 and
A11.4). The infaunal communities were characterized by the predominance of the polychaetes
Prionospio fallax, Monticellina dorsobranchialis and Aricidea sp. The main species
composition of this stratum is given in Table A11.5 and the community variables in Tables
A11.2 and A11.6.
Following is a description of the infaunal communities of the zone most seriously affected by
the oil spill, Zone 2. In the shallowest stratum (71–120 m) we analyzed stations 7, 10 and 13,
all of which were sampled during the five surveys. Station 7 was composed of a muddy
sediment high in organic content, while the sediment of stations 10 and 13 consisted of fine
sands low in organic content (Table A11.1). Once again, polychaetes were the dominant group
in this stratum, reaching an abundance of 88.44 % in station 13 in autumn 2004 (Tables A11.3
and A11.4). The polychaete Prionospio fallax was, once more, the dominant species in the
stratum, along with the echinoderm Amphiura filiformis (Stn. 10) and the polychaetes
Magelona minuta (Stn. 13) and Tharyx sp. (Stn. 10). In the 21–200 m depth stratum (stratum
B) in Zone 2 three stations were studied (8, 11 and 14). The three stations were sampled in the
five study periods (winter 2002, spring and autumn 2003 and spring and autumn 2004). These
stations have a characteristic sediment made up of very fine sands with a moderate organic
content. The polychaetes were the dominant zoological group in this stratum (as high as 88 %
in spring 2004, Stn.8), followed by the crustaceans which accounted for up to 31 % in autumn
2003 (Stn. 11; Tables A11.3 and A11.4). The characteristic species of this stratum were the
peracarid crustacean Ampelisca sp., particularly at station 11, and the polychaetes Prionospio
fallax, P. steentrupii and Monticellona dorsobranchialis (Table A11.5). The community
variables are given in Tables A11.2 and A11.6.
Zona 3 is considered to be a zone of average or moderate impact. In the shallowest stratum,
stratum A (71–120 m), we examined two stations (16 and 19) which are characterized by a
sandy sediment with a low organic content. Again, polychaetes were the typical zoological
group in this stratum (as high as 90.69 % in winter 2002, Stn. 19; Tables A11.3 and A11.4).
Prionospio fallax was the dominant species, reaching a mean abundance of up to 4309
ind•m−2 in station 19. Other characteristic species were the polychaetes Magelona minuta,
Spio decoratus and Levinsenia gracilis. In the 21–200 m depth stratum (stratum B) in Zone 3
we were only able to study one station characterized by a sediment composed of fine sands
and a moderate organic content. Once more, the polychaetes were the stratum’s dominant
group, accounting for over 79% (Tables A11.3 and A11.4). The characteristic species in this
stratum were the polychaetes Prionospio fallax and Monticellina dorsobranchialis. The main
species composition in this stratum is given in Table A11.5 and the community variables in
Tables A11.2 and A11.6.
Temporal evolution of the infaunal communities
In the shallowest area of Zone 1 (stratum A: 70–120 m) in station 1 we observed a decrease in
total abundance during the study period, especially in the main species consisting of spionid
polychaetes and oligochaetes in spring 2003 (Figure A11.4). Species richness and diversity
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ICES BEWG Report 2007
also decreased moderately in spring 2003, but rose sharply in spring 2004. In station 4, on the
other hand, which had a relatively high infaunal abundance (up to 3962 ind•m−2 in spring),
total abundance rose slightly in spring, thanks to the increase in the presence of polychaetes,
particularly, Prionospio fallax (Figure A11.4). Similar to the previous station, species
richness, diversity and evenness decreased slightly in spring (Tables A11.2 and A11.6).
Upon an examination of the stations located in the deepest stratum (stratum B: 121–200 m),
we observed that station 2 showed a modest increase in total abundance in spring 2003 and
2004, owing to the growing number of polychaetes of the genus Aricidea and to Prionospio
fallax (Figure A11.4; Table A11.5). This is the station that exhibited the lowest abundance
values, and never exceeded 1340 ind•m−2 in spring 2004 (Table A11.6). Species richness,
diversity (with a considerably high value – over 5 points) and evenness also underwent a
slight decrease in spring 2003 (Table A11.2). In contrast, station 5, which had a relatively high
infaunal abundance (maximum of 1955 ind•m−2 in winter) exhibited a decrease in total
abundance in spring, especially in the two main species of spionid polychaetes (Prionospio
fallax and P. steenstrupii), and Monticellina dorsobranchialis (Figure A11.4; Tables A11.5).
Unlike the other station in Zone 1, the population parameters for species richness, diversity
(with a considerably high value, above 4.6 points in spring) and evenness increased in spring
2003 (Table A11.2).
Pontevedra transect
ind.m-2
Stratum A
4000
Stratum B
St. 1
St. 2
3000
2000
Others
Crustaceans
1000
Echinoderms
Molluscs
Polychaetes
0
W02
S03
S04
S03
S04
Muros transect
ind.m-2
Stratum A
4000
W02
Stratum B
St. 4
St. 5
3000
2000
Others
Crustaceans
1000
Echinoderms
Molluscs
Polychaetes
0
W02
S03
S04
W02
S03
S04
Figure A11.4. Temporal total abundance (ind•m−2) by taxonomic group in the stations 1, 2, 4 and 5
of the Zone 1. Distribution is shown by transect and depth strata.
Overall, in the zone that suffered the greatest impact from the oil spill (Zone 2), there were
slight variations between the different time periods studied. In general we can point to a slight
increase in the abundance of some of the zoological groups, such as the increasing numbers of
crustaceans (particularly, the amphipods) recorded in stations 10 and 14 (Figure A11.5). We
also witnessed a general rise in the total biomass in most of the stations in the samplings
conducted in 2004. Lastly, worthy of note was the gradual decline in total abundance and
specific richness in the first three samplings (winter 2002, spring and autumn, 2003) of the
stations located in stratum B (121–200 m) of this high-impact zone (stations 8, 11 and 14).
ICES BEWG Report 2007
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In a more detailed examination of the shallowest station (stratum A: 70–120 m) of Zone 2, we
have data available from three stations (7, 10 and 13) which were sampled during five
different seasons (winter 2002, spring 2003 and 2004, and autumn 2003 and 2004), with the
exception of station 7 which was not able to be sampled in winter 2002. Station 7, near the Ría
de Corcubión, presented the lowest values of total abundance in Zone 2. This station did not
exhibit a clear pattern of temporal variation in total abundance, reaching a maximum value of
3985 ind•m−2 in spring 2004; Figure A11.5; Table A11.6). In terms of the temporal evolution
of the main infaunal species, we can highlight the gradual decrease in the abundance of the
polychaete Prionospio steentrupii (from 381 to 0 ind•m−2). Total biomass increased
substantially in spring 2004 owing mainly to the polychaete group with the appearance of a
large number of individuals having a high level of biomass (Sternaspis scutata). Diversity and
evenness reached maximum values in autumn 2003 (H’ = 4.17 and J’ = 0.94; Table A11.2)
and subsequently decreased until the end of the study.
In station 10, in terms of total abundance, low values were observed in winter and autumn,
with increasing abundance in spring. The rise in spring 2004 was the most important in the
entire period under study (up to 6687 ind•m−2). Hence, the variation in this variable did not
follow a clear pattern. As regards faunal groups, there was a gradual increase in the abundance
of the crustacean group until the end of the study, particularly of the amphipods Urothoe
brevicornis (which increased from 126 to 286 ind•m−2) and Perioculodes longimanus (from 11
to 133 ind•m−2), and, to a lesser extent, the amphipod Pontocrates sp. and the group of undet.
Tanaidaceans. In contrast, the polychaete, Magelona minuta and the mollusc Mysella
bidentata declined in number over the course of the study period. Moreover, the total biomass
increased during the first four samplings (maximum 3.96 g•m−2 AFDW, in spring 2004), but
decreased in autumn 2004 (Figure A11.5; Table A11.6). The number of species diminished in
spring 2003, going from 46 to 31 species, and recovering, once again to reach a maximum in
spring 2004 (K = 68). Diversity reached its highest value in spring 2004 (H’ = 4.75) and
evenness gradually increased until it attained a maximum in the same season, similar to
diversity (J’ = 0.78; Table A11.2).
Corcubion transect
-2
ind.m
9000
Stratum A
Stratum B
St. 7
St. 8
6000
Others
3000
Crustaceans
Echinoderms
Molluscs
Polychaetes
0
W02 S03 A03 S04 A04
-2
Muxía transect
ind.m
9000
W02 S03 A03 S04 A04
Stratum A
St. 10
Stratum B
St. 11
6000
Others
3000
Crustaceans
Echinoderms
Molluscs
Polychaetes
0
W02 S03 A03 S04 A04
W02 S03 A03 S04 A04
Figure A11.5. Temporal total abundance (ind•m−2) by taxonomic group in the stations 7, 8, 10 and
11 of the Zone 2. Distribution is shown by transect and depth strata.
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The temporal variation of total abundance by group in station 13 of the highest impact zone
(Zona 2) is presented in figure 6. It had the highest abundance values of all of Zone 2,
reaching 8553 ind•m−2 in spring 2003, five months after the oil spill. It underwent a rapid
decrease in autumn 2003, experiencing a gradual increase until the end of the study,
presenting values of nearly 7600 ind•m−2 (Table A11.6). Some of the polychaetes like
Levinsenia gracilis, Spiophanes bombyx and Monticellina dorsobranchialis, along with the
bivalve mollusc Tellina pygmaea exhibited an increasing pattern over time, which might
suggest that the initial effect on these species was negative, and then they later went on to
recover their abundance levels. Similarly, other species, whose values in the early studies were
relatively high, decreased progressively over time (i.e. the polychaetes Prionospio steenstrupii
and Paradoneis lyra). Both of these statements are risky, since the abundance values of these
species prior to the oil spill are not known. Similar to what occurred in station 7, the total
biomass tended to increase, exhibiting a pronounced maximum in autumn 2003 which may be
attributed to the presence of large-sized molluscs and crustaceans. The number of species was
relatively constant over the whole period with the exception of spring 2004 when the
maximum value was attained (K = 98). Diversity and evenness reached maximum values in
spring 2003 (H’ = 4.97 y J’ = 0.83; Table A11.2) and then started to decrease little by little
until the end of the study.
-2
Laxe transect
ind.m
9000
Stratum A
St. 13
Stratum B
St. 14
6000
Others
3000
Crustaceans
Echinoderms
Molluscs
Polychaetes
0
W02 S03 A03 S04 A04
W02 S03 A03 S04 A04
Figure A11.6. Temporal total abundance (ind•m−2) by taxonomic group in the stations 13 and 14 of
the Zone 2. Distribution is shown by depth strata.
Upon an examination of the stations located in the deepest stratum (stratum B: 121–200 m) we
observed that at station 8, which was sampled in five different seasons, there was a gradual
decrease in total abundance during the first three samplings, from 1897 ind•m−2 in winter 2002
to 1238 ind•m−2 in autumn 2003. Subsequently, in spring 2004 there was an increase, leading
to the maximum total abundance for the entire period studied (2711 ind•m−2; Figure A11.5;
Table A11.6). No clear distribution pattern was observed in the main infaunal species. The
dominant specie Prionospio fallax, which declined initially during the early samplings,
recovered its abundance in spring 2004 (reaching up to 356 ind•m−2;). Similarly, P.
steenstrupii, which at first increased in, started to decrease as of spring 2003 going from 324
to 114 ind•m−2;. Infaunal biomass behaved irregularly, with high values being recorded in the
two autumn samplings (máx 4.67 g•m−2 AFDW, in 2004; Table A11.6) and very low values in
the spring samplings. The number of species diminished during the first three samplings, and
then rose sharply in spring 2004, reaching the maximum of the period under study (K = 60).
Diversity, which was high, ranged in value from 4.02 to 4.90, both in spring, 2003 and 2004,
respectively. Evenness remained relatively stable at around 0.83 points, presenting its
maximum value of 0.92 in the last sampling (Table A11.2).
Other stations studied in this deep stratum of Zone 2 were numbers 11 and 14, which were
sampled in the five time periods and exhibited a similar temporal variation pattern. Initially, in
Station 11 total abundance decreased until autumn 2003 (from 3555 to 2877 ind•m−2) owing
mainly to the diminishing numbers of the amphipod crustacean Ampelisca sp. (from 869 to
610 ind•m−2), which was the dominant species in the community, and a decrease in the
ICES BEWG Report 2007
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polychaetes Prionospio fallax and Monticellina dorsobranchialis (Figure A11.5). Later,
however, there was a substantial increase in abundance and total biomass in spring 2004 (4483
ind•m−2 and 3.96 g•m−2 AFDW, respectively), only to decrease again during the last sampling
(Table A11.6). Specific richness exhibited a similar temporal evolution, with a maximum in
spring 2004 of 67 species. Diversity and evenness, which behaved in an irregular fashion,
reached their highest values in autumn 2004 (H’ = 4.35 and J’ = 0.86; Table A11.2).
Similar to what occurred in station 11, in station 14 we initially observed a slight drop in total
abundance until autumn 2003 and then a subsequent rapid increase of this variable and total
biomass in spring 2004 attaining values of 4208 ind•m−2 and 6.81 g•m−2 AFDW, respectively.
Afterwards, the two variables decreased in autumn 2004, which was the last month of
sampling (Figure A11.6, Table A11.6). This increase in abundance coincided with a major
increase in the peracarid group (up to 489 ind•m−2 in spring 2004), which are considered to be
sensitive to hydrocarbon contamination and would therefore indicate that the early samplings
might be affected by the oil spill. Amphipods are considered to be the most sensitive species
to hydrocarbons in sediments (Dauvin, 1987; Dauvin and Gentil, 1990; Parra et al., 1997b;
Gómez Gesteira and Dauvin, 2000)
Similarly, in the two previous stations, the number of species declined during the first three
samplings and then rose substantially in spring 2004 when the maximum value was reached
(K = 83), while diversity and evenness had relatively constant values throughout the period
under study, with maximum values of 4.86 and 0.89, in spring and autumn 2003, respectively
(Table A11.2).
-2
Caión transect
ind.m
Stratum A
Stratum B
15000
St. 16
St. 17
12000
9000
6000
Others
Crustaceans
3000
Echinoderms
Molluscs
Polychaetes
0
W02 S03 A03 S04 A04
ind.m -2
15000
W02 S03 A03 S04 A04
Coruña transect
Stratum
A
St. 19
12000
9000
6000
Others
Crustaceans
3000
Echinoderms
Molluscs
Polychaetes
0
W02
S03
A03
S04
A04
Figure A11.7. Temporal total abundance (ind•m−2) by taxonomic group in the stations 16, 17 and
19 of the Zone 3. Distribution is shown by transect and depth strata.
In the moderately-impacted zone (Zone 3), we only examined the temporal evolution (in five
periods) of the infaunal communities inhabiting the continental shelf in two stations belonging
to shallow stratum A (Stns. 16 y 19) and one in the deepest stratum B, (Stn. 17). In general, a
progressive decrease was seen in the total abundance during the first four samplings (W02,
S03, A03 and S04) and in richness during the first three samplings, in stations belonging to
stratum A. In contrast, we recorded a gradual increase in the abundance of the crustacean
group, particularly amphipods, in these stations (Figure A11.7).
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In a more detailed examination of the shallowest station number 16 of Zone 3 (stratum A: 70–
120 m), we can see a gradual decline in total infaunal abundance during the first four
samplings (from 7875 to 5277 ind•m−2), followed by a major rise in this variable which
reached 14878 ind•m−2-the highest value recorded in the whole study. On the other hand, the
amphipod group underwent a gradual increase throughout the study period, particularly
Ampelisca spp. and the family Phoxocephalidae, which could mean that this crustacean group
might be negatively affected by the Prestige oil spill. The assumption of this hypothesis is
very complicated owing to the lack of available data prior to the spill. Total biomass was
dominated by the polychaetes and its temporal variation did not follow any specific pattern,
reaching a maximum of 4.43 g•m−2 AFDW in autumn 2003 (Table A11.6). The behavior of
species number was similar to that of the stations located in the same stratum of Zone 2, with
a maximum of 81 species in spring 2004. Diversity and evenness were relatively stable and
attained their highest values in spring 2004 and autumn 2003, respectively (H’ = 4.53 and J’ =
0.73; Table A11.2).
Like the station discussed above, in terms of total abundance, station 19 (stratum A, Zone 3),
underwent a sharp drop during the first four samplings, going from an abundance of 8230
ind•m−2 in winter 2002 to 4356 ind•m−2 in spring 2004. The total abundance later increased
considerably in autumn 2004, the last month of sampling, when a value of 11220 ind•m−2 was
attained. Again, we must underline the importance of the gradual increase in the amphipod
group (Ampelisca spp.) and the cumaceans, owing to their possible link to the oil spill (Figure
A11.7). With the exception of the total biomass value during the first month of sampling
(owing to the presence of a large-sized echinoderm), we can see that this variable increased
gradually throughout the entire study period, with a final value of around 4.60 g•m−2 AFDW
(Table A11.6) The variation in number of species behaved similarly to station 16, although
with higher values, reaching a maximum of 103 species in spring de 2004. This is the highest
value of all the stations in this study. Diversity and evenness attained their maximum values in
spring 2004 and autumn 2003 respectively (H’ = 4.97 y J’ = 0.83; Table A11.2).
Lastly, station 17 located in stratum B of Zone 3, exhibited the lowest total abundance and
total biomass values in this zone over the course of the whole study. The temporal variation of
total abundance was irregular, presenting a maximum of 3677 ind•m−2 in spring 2004 and the
highest values for variation in total biomass were found in the last two seasons sampled (a
maximum of 2.03 g•m−2 AFDW in spring 2004; Figure A11.7; Table A11.6). The number of
species was similar to that of the other stations in Zone 3, with a maximum of 79 species in
spring 2004. Diversity and evenness were relatively stable, reaching their highest values in
spring 2004 and autumn 2003, respectively (H’ = 5.21 and J’ = 0.81; Table A11.2).
CONCLUSIONS
The sediment is dominated by fine sands having a low organic content. No temporal changes
that may be attributed to the impact of the oil spill were observed in the sedimentary variables.
The temporal evolution of the structural parameters of Zone 1 would not suggest that they
suffered any effect from the oil spill. In Zone 2 by contrast, we found an increase in the
abundance of the crustacean group (amphipods) in stations 10 and 14, a general increase in the
total biomass in the 2004 samplings and a gradual decline in the total abundance and specific
richness during the first three samplings of the stations located in stratum B (stations 8, 11 and
14). Zone 3 underwent a progressive decrease in total abundance during the first four
samplings and of richness during the first three samplings in the stations belonging to stratum
A (stations 16 and 19). In contrast, a gradual increase in the abundance of the crustacean
group (amphipods) was recorded in the same stations.
Generally speaking, none of the zones showed any major changes in either the temporal
pattern or the structure of the infaunal community. We did not see any marked increase in
ICES BEWG Report 2007
| 69
opportunistic species or species favoured by the oil spill (i.e., capitelid and spionids
polychaetes; Pearson, 1975; Pearson and Rosenberg, 1978; Plante-Cuny et al., 1993). Owing
to the lack of previous data, we are unable to confirm whether or not mortalities have occurred
in species that are sensitive to hydrocarbon contamination (i.e. echinoderms and peracarid
crustaceans), although the increasing crustacean populations in some stations could be related
to the oil spill.
BIBLIOGRAPHY
Buchanan, J. B. 1984. Sediment analysis. In Methods for the study of marine benthos, pp. 41–
65. Ed. by N. A. Holme and A. D. McIntyre Blackwell Scientific Publications, Oxford.
Dauvin, J.-C. 1987. Evolution à long terme (1978–1986) des populations d’amphipodes des
sables fins de la Pierre Noire (Baie de Morlaix, Manche Occidentale) après la catastrophe
de l’Amoco Cadiz. Mar. Environ. Res., 21: 247–273.
Dauvin, J.-C. and F. Gentil. 1990. Conditions of the peracarid populations of subtidal
communities in Northern Brittany ten years after the Amoco Cadiz oil spill. Mar. Pollut.
Bull., 21 (3): 123–130.
Gómez Gesteira, J. L., and Dauvin, J.-C., 2000. Amphipods are good bioindicators of the
impact of oil spills on soft-bottom macrobenthic communities. Mar. Poll. Bull. 40, 1017–
1027.
López-Jamar, E., Bode, A., Parra, S., and Vázquez, A. 1996b. Consecuencias del vertido de
crudo del Aegean Sea sobre la macrofauna bentónica submareal. In Seguimiento de la
contaminación producida por el accidente del buque Aegean Sea, 109–135 pp. Ed. by J.
Ros. Ministerio de Medio Ambiente, Serie monografías. Madrid.
Parra, S., and López-Jamar, E. 1997. Cambios en el ciclo temporal de algunas especies
endofaunales como consecuencia del vertido del petrolero Aegean Sea. Publ. Esp
Parra, S., López-Jamar, E., González, J. J. and Nunes, T. 1997. Final report on the effects of
the Aegean Sea oil spill on the subtidal macroinfauna. In Report of the Benthos Ecology
Working Group, 23–26 April 1997, Gdynia, Polonia. ICES CM 1997/L:7. 85 pp.
Parra, S., Frutos, I., Serrano, A., Sánchez, F., Preciado, I., and Velasco, F. 2005. The impact
of the Prestige oil spill on the infaunal and hyperbenthic communities of the Continental
Shelf off Atlantic NW Iberian waters (Galicia). ICES Benthos Ecology Working Group.
April 2005. Copenhagen, Dinamarca.
Pearson, T. H. 1975. The benthic ecology of Loch Linnhe and Loch Eil, a sea-loch system on
the west coast of Scotland. IV. Changes in the benthic fauna attributable to organic
enrichment. J. Exp. Mar. Biol. Ecol., 20: 1–41.
Pearson, T. H., and Rosenberg, R., 1978. Macrobenthic succession in relation to organic
enrichment and pollution of the marine environment. Oceanogr. Mar. Biol. Ann. Rev. 16,
229–311.
Plante-Cuny, M. R., Salen-Picard, C., Grenz, C., Plante, R., Alliot, E. and Barranguet, C.
1993. Experimental field study of the effects of crude oil, drill cuttings and natural
biodeposits on microphyto- and macrozoobenthic communities in a Mediterranean area.
Mar. Biol., 117: 355–366.
Sánchez, F. 2003. Presencia y cuantificación del fuel sedimentado en las plataformas de
Galicia y mar Cantábrico. IEO Prestige web report nº 14:
www.ieo.es/prestige/informe14.htm, 7 pp.
Sánchez, F., Parra, S., Serrano, A., and Velasco, F. 2003a. Informe técnico sobre el vertido del
Prestige nº 6 (www.ieo.es), 26 p.
Sánchez, F., Serrano, A., Parra, S., Velasco, F., Punzón, A., and Frutos, I. 2003b. Prestige oil
spill on the Northh Spanish coast: preliminary Spanish Oceanographic Institute (IEO)
70 |
ICES BEWG Report 2007
impact studies on the benthic habitat. ICES Benthos Ecology Working Group. Abril 2003.
Fort Pierce, Florida (USA).
Sánchez, F., Serrano, A., Parra, S., Frutos, I., Velasco, F., and Punzón, A. 2004. The impact of
the Prestige oil spill on the benthic and demersal communities of the Continental Shelf off
Galicia and in the Cantabrian Sea. ICES Benthos Ecology Working Group. Abril 2004.
AZTI, Pasaia, San Sebastián.
Tables
Table A11.1. Sediment variables. Symbols: % O.M.: organic content; Q50: mean diameter (Φ
Units and µm); S0: sorting coefficient (√Q25/Q75).
Station
Depth (m) Q50 (phi)
Q50 (μm)
% O.M.
S0
1
101
4.62 ± 0.03
41 ± 1
4.02 ± 0.43
1.90 ± 0.12
2
155
2.58 ± 0.04
167 ± 4
3.60 ± 0.21
1.27 ± 0.02
3
233
3.55
85
3.00
1.33
4
100
3.93 ± 0.22
66 ± 10
2.98 ± 0.36
1.68 ± 0.09
5
137
2.60 ± 0.08
165 ± 9
2.40 ± 0.56
1.31 ± 0.02
6
244
2.66
158
1.92
1.30
7
106
4.63 ± 0.21
41 ± 6
6.35 ± 0.14
2.18 ± 0.47
8
154
3.07 ± 0.20
120 ± 17
2.24 ± 0.37
1.50 ± 0.02
9
248
3.51
88
2.63
1.29
10
78
2.64 ± 0.10
161 ± 11
3.34 ± 0.30
1.37 ± 0.05
11
168
3.66 ± 0.08
79 ± 4
3.38 ± 0.23
1.65 ± 0.17
12
250
3.00
125
3.24
1.99
13
86
3.06 ± 0.05
120 ± 4
3.32 ± 0.26
1.71 ± 0.05
14
151
3.17 ± 0.12
112 ± 10
3.15 ± 0.49
1.62 ± 0.07
15
259
2.73
151
3.26
1.68
16
85
3.55 ± 0.20
86 ± 12
4.18 ± 0.36
1.68 ± 0.13
17
150
3.59 ± 0.30
85 ± 17
3.99 ± 0.34
2.46 ± 0.25
18
239
2.57
168
4.23
1.91
19
90
2.77 ± 0.13
147 ± 13
1.20 ± 0.11
1.36 ± 0.06
20
154
3.05 ± 0.24
122 ± 21
3.27 ± 0.23
1.90 ± 0.10
21
284
3.51
88
3.09
2.19
22
175
2.70 ± 0.17
155 ± 18
2.58 ± 0.32
1.37 ± 0.05
23
282
2.50
177
3.76
1.42
ICES BEWG Report 2007
| 71
Table A11.2. Macrofauna richness (K), diversity (H’) and evenness (J’) at each station by season
(W: winter; S: spring; A: autumn).
K
H'
J'
W02 S03 A03 S04 A04
W02 S03 A03 S04 A04
W02 S03 A03 S04 A04
1
22
18
-
30
2.84 2.54 -
3.33 -
0.64 0.61 -
0.68 -
2
28
27
-
64
-
4.12 4.05 -
5.16 -
0.86 0.85 -
0.86 -
4
36
30
-
-
-
3.15 2.62 -
-
-
0.61 0.53 -
-
-
-
-
0.79 0.89 -
-
-
Season
Station
-
5
30
35
-
-
-
3.89 4.57 -
7
-
21
22
50
15
-
8
45
29
27
60
37
4.56 4.02 4.16 4.90 4.78
0.83 0.83 0.87 0.83 0.92
10
44
31
47
68
56
3.78 3.60 4.25 4.75 4.22
0.69 0.73 0.76 0.78 0.73
11
41
37
23
67
34
3.90 4.06 3.27 4.16 4.35
0.73 0.78 0.72 0.69 0.86
13
66
64
63
98
53
4.04 3.99 4.97 4.73 3.70
0.67 0.66 0.83 0.72 0.65
14
48
43
40
83
42
4.57 4.81 4.86 5.06 4.70
0.82 0.89 0.91 0.79 0.87
16
72
50
51
81
68
3.81 3.55 4.13 4.53 3.59
0.61 0.63 0.73 0.71 0.59
17
48
31
39
79
31
4.59 4.51 4.57 5.15 4.34
0.82 0.91 0.86 0.82 0.88
19
81
71
58
103 72
3.53 4.02 4.72 5.21 3.96
0.56 0.65 0.81 0.78 0.64
3.05 4.17 4.09 2.62
-
0.69 0.94 0.72 0.67
Table A11.3. Macroinfaunal percentage made up of each group (P: polychaetes; M: molluscs; E:
echinoderms) of total abundance at each station by season (W: winter; S: spring; A: autumn).
%P
Season W02 S03 A03 S04 A04
%M
%E
W02 S03 A03 S04 A04
W02 S03 A03 S04 A04
Station
1
77.11 82.89 -
88.99 -
5.42 10.53 -
1.38 -
0.60 0.00 -
0.00 -
2
91.57 87.88 -
67.30 -
0.00 1.52 -
2.37 -
1.20 1.52 -
0.47 -
4
86.67 92.31 -
-
-
4.76 2.88 -
-
-
0.00 0.00 -
-
-
5
86.55 78.35 -
-
-
3.51 7.22 -
-
-
0.58 0.00 -
-
-
7
-
8
82.53 80.22 80.00 88.76 78.72 4.22 9.89 3.08 0.47 5.32
0.60 1.10 0.00 0.23 2.13
10
66.06 53.54 45.66 49.11 50.71 10.41 11.06 7.55 9.05 6.55
10.18 19.47 12.83 9.37 13.39
11
65.23 70.20 65.17 67.56 71.82 4.30 3.31 1.12 1.84 5.45
0.00 0.00 0.00 0.00 0.00
13
85.02 84.19 76.05 83.81 88.44 5.62 6.90 8.74 7.74 6.53
3.75 4.45 4.53 1.12 0.25
14
73.80 70.99 55.26 70.69 76.34 7.42 18.32 20.18 10.73 6.87
0.00 0.76 0.00 0.00 0.00
16
76.20 66.16 78.39 72.20 83.74 16.84 13.74 10.53 16.00 7.68
1.45 16.03 1.11 1.44 0.13
17
77.13 62.37 79.83 78.93 79.22 13.18 25.81 10.92 7.25 12.99 0.39 0.00 0.00 0.00 0.00
19
90.69 82.10 75.18 77.26 84.04 3.75 4.55 4.74 4.08 2.89
77.42 65.91 77.69 42.06 -
16.94 27.27 15.46 11.21 -
0.00 0.00 0.00 0.00
1.53 3.41 6.20 4.96 0.51
72 |
ICES BEWG Report 2007
Table A11.4. Macroinfaunal percentage made up of each group (C: crustaceans; O: others minor
groups) of total abundance at each station by season (W: winter; S: spring; A: autumn).
%C
Season
%O
W02
S03
A03
S04
A04
W02
S03
A03
S04
A04
1
0.00
0.00
-
3.67
-
16.87
6.58
-
5.96
-
2
1.20
6.06
-
28.91
-
6.02
3.03
-
0.95
-
4
0.95
0.96
-
-
-
7.62
3.85
-
-
-
5
1.75
3.09
-
-
-
7.60
11.34
-
-
-
7
-
5.65
4.55
3.35
0.00
-
0.00
2.27
3.51
46.73
8
2.41
7.69
6.15
5.62
8.51
10.24
1.10
10.77
4.92
5.32
10
3.85
4.42
5.66
12.60
10.54
9.50
11.50
28.30
19.87
18.80
11
27.15
25.17
31.46
27.20
20.00
3.31
1.32
2.25
3.40
2.73
13
2.62
2.00
4.21
3.77
2.01
3.00
2.45
6.47
3.56
2.76
14
5.68
5.34
12.28
12.39
13.74
13.10
4.58
12.28
6.19
3.05
16
1.89
2.29
3.32
7.22
4.74
3.63
1.78
6.65
3.13
3.71
17
3.88
5.38
5.88
9.50
3.90
5.43
6.45
3.36
4.32
3.90
19
1.25
6.25
8.76
10.64
5.26
2.78
3.69
5.11
3.06
7.30
Station
ICES BEWG Report 2007
| 73
Table A11.5. The most important macroinfaunal taxa (ten most important species by station, in
abundance; ind•m−2).
ZONE
Station
1
2
3
1
2
4
5
7
8
10
11
13
14
16
17
19
Prionospio
fallax
808
250
2079
250
727
284
1026
348
2182
337
3412
560
4309
Magelona
minuta
.
.
.
.
109
99
176
70
501
197
405
.
606
Prionospio
steenstrupii
131
.
172
61
171
218
.
517
211
223
.
103
.
Monticellina
dorsobranchialis
.
43
160
234
71
120
.
225
292
226
.
286
.
Lumbrineris
gracilis
31
.
.
.
101
.
.
.
472
.
212
.
240
Levinsenia
gracilis
60
.
.
.
64
64
.
43
221
.
428
.
.
Spio decoratus
.
.
.
.
.
.
.
.
.
.
512
.
103
Aricidea sp.
.
130
173
250
.
.
.
.
.
.
.
.
.
Spiophanes
bombyx
.
.
.
.
.
.
120
.
147
.
231
.
.
Mediomastus
fragilis
31
58
54
.
.
52
.
97
.
116
.
.
.
Tharyx sp.
.
.
.
.
.
.
407
.
.
.
.
.
.
Archiannelida
undet.
.
.
.
.
137
.
.
.
.
.
.
263
.
Paraonidae
undet.
.
89
248
61
.
.
.
.
.
.
.
.
.
Aricidea
claudiae
.
.
.
.
.
88
.
.
292
.
.
.
.
Aricidea fragilis
mediterranea
.
.
.
.
.
.
.
.
.
.
.
.
366
Ampharete
finmarchica
.
.
.
.
.
83
.
106
.
.
.
137
.
Magelona
wilsoni
.
33
183
71
.
.
.
.
.
.
.
.
.
Galatowenia
oculata
.
68
.
.
.
.
.
97
.
79
.
.
.
Ampharetidae
undet.
.
.
.
162
.
48
.
.
.
.
.
.
.
Paradoneis lyra
.
.
.
.
.
.
.
.
178
.
.
.
.
Aphonuphis
bilineata
.
.
.
.
.
.
.
.
.
.
.
.
137
Aricidea
claudiae
.
.
.
.
.
.
.
.
.
.
.
.
126
Aricidea
catherinae
.
.
.
.
.
.
.
.
.
.
.
.
126
Sternaspis
scutata
40
.
.
.
78
.
.
.
.
.
.
.
.
Ariciidae undet.
.
.
.
.
.
.
.
.
.
.
.
.
103
Chone
filicaudata
.
.
.
.
.
.
.
.
.
.
.
91
.
Aricidea laubieri
.
.
.
.
.
.
.
.
.
.
.
80
.
Exogone hebes
.
.
.
.
.
.
78
.
.
.
.
.
.
Species
Polychaetes
74 |
ICES BEWG Report 2007
1
ZONE
2
3
Station
1
2
4
5
7
8
10
11
13
14
16
17
19
Hyalinoecia
brementi
.
.
.
55
.
.
.
.
.
.
.
.
.
Cirratulidae
undet.
.
48
.
.
.
.
.
.
.
.
.
.
.
Notomastus
latericeus
37
.
.
.
.
.
.
.
.
.
.
.
.
Thyasira
obsoleta
.
.
.
.
.
.
.
.
.
100
244
160
.
Tellina
pygmaea
.
.
.
.
.
.
.
.
.
.
352
.
.
Mysella
bidentata
.
.
.
.
.
.
228
.
.
.
.
.
.
Onova vitrea
.
.
.
.
183
.
.
.
.
.
.
.
.
Abra sp.
137
.
.
.
.
.
.
.
.
.
.
.
.
Veneridae
undet.
.
.
.
.
.
.
.
.
.
.
.
114
.
Thyasira
ferruginea
.
.
.
.
97
.
.
.
.
.
.
.
.
Bathyarca
glacialis
.
.
.
.
.
.
.
.
.
76
.
.
.
Thyasira sp.
.
.
44
.
.
.
.
.
.
.
.
.
.
Amphiura
filiformis
.
.
.
.
.
.
596
.
.
.
.
.
.
Ophiurid undet.
.
.
.
.
.
.
.
.
.
.
318
.
.
Ampelisca sp.
.
.
.
.
.
.
.
679
.
97
.
.
.
Euphausid
undet.
.
171
.
.
.
.
.
.
.
.
.
.
.
Urothoe
brevicornis
.
.
.
.
.
.
161
.
.
.
.
.
.
Callianassa
subterranea
.
70
.
.
.
.
.
.
.
.
.
.
.
Nemertinos
undet.
80
.
124
57
.
65
201
62
187
127
249
137
183
Oligochaete
undet.
117
.
126
.
.
.
679
.
.
.
.
.
.
Onchnesoma
steentrupii
.
.
.
101
.
.
.
.
.
.
.
.
.
Molluscs
Echinoderms
Crustaceans
Others
ICES BEWG Report 2007
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Table A11.6. Macroinfaunal total abundance (ind•m−2) and biomass (g•m−2) at each station by
season (W: winter; S: spring; A: autumn).
TOTAL ABUNDANCE
TOTAL BIOMASS
-2
-2
Ind·m
Season
g·m
W02
S03
A03
S04
A04
W02
S03
A03
S04
A04
1
1897
1482
-
1384
-
-
-
-
5.54
-
2
1186
1257
-
1340
-
-
-
-
2.90
-
4
3601
3962
-
-
-
-
-
-
-
-
5
1955
1848
-
-
-
-
-
-
-
-
7
-
2362
838
3985
1105
-
1.08
1.55
8.77
1.56
8
1897
1734
1238
2711
1791
1.42
0.56
3.18
1.32
4.67
10
5052
4305
5048
3931
6687
2.20
2.95
3.58
3.96
2.52
11
3552
2877
1695
4483
2096
0.42
0.66
1.40
3.96
0.70
13
6104
8553
5886
6236
7582
1.73
1.63
7.82
3.58
1.86
14
2617
2496
2172
4204
2496
0.79
0.77
0.70
6.81
1.55
16
7875
7487
6877
5277
14878
2.77
2.57
4.43
4.05
2.49
17
2949
1772
2267
3677
1467
0.36
0.14
0.49
2.03
0.96
19
8230
6706
5220
4356
11220
5.66
2.53
5.12
4.67
4.63
Station
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Annex 12: Sp at i al a nd t e m p ora l c h a ng es i n b ent h i c
co m m u ni t ies o f t h e Ga li c ia n co nt i ne nt a l s he l f a f t e r t h e
P r e s t i g e oi l s pi ll
ICES BEWG Report 2007
Annex 13: Mo n it ori ng t he P r e s t i g e oi l sp il l im pa cts o n some
k e y s p e c i e s o f t he N ort he r n Ib eria n s he lf
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Annex 14: L i s t o f m et r i c s ( u p d a t e d f r o m S G S O B S 2 0 0 4 )
Univariate indices:
Shannon-Wiener Diversity Index
Shannon, C.E. and Weaver, W., 1949. The Mathematical Theory of Communication. The
University of Illinois Press, Urbana, Illinois, USA, 115 pp.
Benthic Pollution Index (BPI)
Leppäkoski, E. 1975. Assessment of degree of pollution on the basis of macrozoobenthos in
marine and brackish-water environments. Acta Academiae Aboensis, Ser., B 35: 1–89.
Infauna Trophic Index (ITI)
Word, J. Q. 1979. The Infaunal Trophic Index. Sth Calif. Coast. Water Research Project.
Annual Report, El Segundo, California. 19–39.
Word, J. Q. 1980. Classification of benthic invertebrates into Infaunal Trophic Index feeding
groups. In Coastal Water Research Project Biennial Report 1979–1980, 103-121 pp.
SCCWRP, Long Beach, California, USA,
ABC curves
Warwick, R. and Clarke, K.R. 1994. Relating the ABC: taxonomic changes and
abundance/biomass relationship in disturbed benthic communities. Marine Biology, 118
(4): 739–744.
Annelid Index of Pollution
Bellan, G. 1980. Relationships of pollution to rocky substratum polychaetes on the French
Mediterranean coast. Marine Pollution Bulletin, 11: 318–321.
Shannon Wiener Evenness Proportion Index
McManus, J.W., and Pauly, D., 1990. Measuring ecological stress: variations on a theme by
R.M. Warwick. Marine Biology, 106: 305–308.
Taxonomic diversity index and Taxonomic distinctness
Warwick, R.M., and Clarke, K.R., 1995. New "biodiversity" measures reveal a decrease in
taxonomic distinctness with increasing stress. Marine Ecology Progress Series, 129: 301–
305.
Ecological Evaluation Index (EEI)
Orfanidis, S., Panayotidis, P., and Stamatis, N. 2001. Ecological evaluation of transitional and
coastal waters: a marine benthic macrophytes-based model. Mediterranean Marine
Science, 2: 45–65.
Hurlbert Index
Hurlbert, S. H. 1971. The non-concept of species diversity: A critique and alternative
parameters. Ecology 52, 577–586.
Coastal Endofaunic Evaluation Index (I2EC)
Grall, J., and Glemarec, M. 2003. L’indice d’évaluation de l’endofaune côtiere. In
Bioévaluation de la qualité environnementale des sediments portuaires et des zones
d’immersion, pp. 51–85. Ed. by C. Alzieu (coord.). Ifremer.
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Benthic opportunistic polychaetes amphipods index (BOPA)
Gomez Gesteira, L., and Dauvin, J. C. 2000. Amphipods are good bioindicators of te impact
of opil spills on soft-bottom macrobenthic communities. Marine Pollution Bulletin 40:
1017–1027.
Dauvin, J. C. and Ruellet, T. 2007. Polychaete/amphipod ratio revisited. Marine Pollution
Bulletin, 55: 215–224.
Several other simple univariate metrics are of common use e.g. species number, number of
individuals, biomass.
Multimetric indices:
Pollution Coefficient
Satsmadjis, J. 1982. Analysis of benthic data and measurement of pollution. Revue
internationale d’Océanographie Medicale, 66–67: 103–107.
Satsmadjis, J. 1985. Comparison of indicators of pollution in the Mediterranean. Marine
Pollution Bulletin, 16: 395–400.
Biological Quality Index (BQI)
Jeffrey, D. W., Wilson, J. G., Harris, C. R., and Tomlinson, D.L. 1985. The application of two
simple indices to Irish estuary pollution status. Estuarine management and quality
assessment. Plenum Press, London. 147–165 pp.
Infauna Ratio-to-Reference of Sediment Quality Triad (RTR)
Chapman, P. M., Dexter, R. N. and Long. E. R. 1987. Synoptic measures of sediment
contamination, toxicity and infauna community composition (the Sediment Quality Triad)
in San Francisco Bay. Marine Ecology Progress Series, 37: 75–96.
Biotic Index
Majeed, S.A., 1987. Organic matter and biotic indices on the beaches of North Brittany.
Marine Pollution Bulletin, 18: 490–495.
Grall, J., and Glémarec, M. 1997. Using biotic indices to estimate macrobenthic community
perturbations in the bay of Brest. Estuarine, Coastal and Shelf Science, 44: 43–53.
Hily, C. 1984. Variabilité de la macrofaune benthique dans les milieux hypertrophiques de la
Rade de Brest. Thèse de Doctorat d’Etat, Univ. Bretagne Occidentale. Vol. 1: 359 pp.,
Vol. 2: 337 pp.
Hily, C., Le Bris, H., and Glémarec, M. 1986. Impacts biologiques des émissaires urbains sur
les écosystèmes benthiques. Oceanis, 12: 419–426.
Benthic Index of Estuarine Condition
Weisberg, S. B., Frithsen, J. B., Holland, A. F., Paul, J. F., Scott, K. J., Summers, J. K.,
Wilson H. T., Heimbuch, D. G., Gerritsen, J., Schimmel, S. C. and Latimer, R. W., 1993.
Virginian Province Demonstration Project Report, EMAP-Estuaries, 1990. EPA/620/R93/006, Office of Research and Development, USEPA, Washington, DC., USA.
Schimmel, S. C., Melzian, B. D., Campbell, D. E., Benyi, S. J., Rosen, J. S. and. Buffum, H.
W. 1994. Statistical Summary: EMAP- Estuaries Virginian Province, 1991. Office of
Research and Development, Environmental Research Laboratory, USEPA, Narragansett,
Rhode Island, USA, 77 pp.
Strobel, C. J., Buffum, H. W., Benyi, S. J., Petrocelli, E. A., Reifsteck, D. R. and Keith, D. J.
1995. Statistical Summary. EMAP- Estuaries Virginian Province – 1990 to 1993.
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National Health Environmental Effects Research Laboratory, Atlantic Ecology Division,
USEPA, Narragansett, RI, USA, 72 pp.
Benthic condition Index (BCI)
Engle, V. D., Summers, J. K., and Gaston, G. R. 1994. A benthic index of environmental
condition of Gulf of Mexico estuaries. Estuaries, 17: 372–384.
Engle, V. D. and Summers, J.K. 1999. Refinement, validation and application of a benthic
condition index for Northern Gulf of Mexico estuaries. Estuaries, 22: 624–635.
Paul, J.F., Scott, K. J., Campbell, D. E., Gentile, J. H., Strobel, C. S., Valente, R. M.,
Weisberg, S. B., Holland, A. F., and Ranasinghe, J.A. 2001. Developing and applying a
benthic index of estuarine condition for the Virginian biogeographic province. Ecological
Indicators, 1: 83–99.
Benthic Index of biotic integrity (B-IBI)
Ranasinghe, J.A., Weisberg, S.B., Dauer, D.M., Schaffner, L.C., Diaz, R.J. and Frithsen, J.B.,
1994. Chesapeake Bay Benthic Community Restoration Goals. CBP/TRS 107/94,
Chesapeake Bay program Office, USEPA, Annapolis, Maryland, USA, 49 pp.
Weisberg, S. B., Ranasinghe, J. A. 1997. An estuarine benthic index of biotic integrity (BBY) for Chesapeake Bay. Estuaries, 20: 149–158.
Van Dolah, R. F., Hyland, J. L., Holland, A. F., Rosen, J. S., and Snoots, T. R. 1999. A
benthic index of biological integrity for assessing habitat quality in estuaries of the
southeastern USA. Marine Environmental Research, 48: 269–283.
Llansó, R. J., Scott, L. C., Dauer, D. M., Hyland, J. L., Russell, D. E. 2002. An estuarine
benthic index of biotic integrity for the mid-Atlantic region of the United States. I.
Classification of assemblages and habitat definition. Estuaries, 25: 1219–1230.
Llansó, R. J., Scott, L. C., Hyland, J. L., Dauer, D. M., Russell, D. E., and Kutz, F. W. 2002.
An estuarine benthic index of biotic integrity for the mid-Atlantic region of the United
States. II. Index development. Estuaries, 25: 1231–1242.
AMBI (AZTI Marine Biotic Index)
Borja, A., Franco, J., and Pérez, V. 2000. A marine biotic index to establish the ecological
quality of soft-bottom benthos within European estuarine and coastal environments.
Marine Pollution Bulletin, 40: 1100–1114.
Borja, A., Muxika, I., and Franco, J. 2003. The application of a Marine Biotic Index to
different impact sources affecting soft-bottom benthic communities along European
coasts. Marine Pollution Bulletin, 46: 835–845.
Borja, A., Franco, J., and Muxika, I. 2004. The Biotic Indices and the Water Framework
Directive: the required consensus in the new benthic monitoring tools. Marine Pollution
Bulletin, 48: 405–408.
Bentix
Simboura, N., and Zenetos, A. 2002. Benthic indicators to use in ecological quality
classification of Mediterranean soft bottom marine ecosystems, including a new biotic
index. Mediterranean Marine Science, 3: 77–111.
Ecofunctional Quality Index (EQI)
Fano, E.A., Mistri, M., and Rossi, R. 2003. The ecofunctional quality index (EQI): a new tool
for assessing lagoonal ecosystem impairment. Estuarine, Coastal and Shelf Science, 56:
709–716.
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Indicator Species Index
Rygg, B. 2002. Indicator species index for assessing benthic ecological quality in marine
waters of Norway. Norwegian Institute for Water Research, Report Nº 40114: 1–32.
Benthic Quality Index
Rosenberg, R., Blomqvist, M., Nilsson, H. C., Dimming, A., 2004. Marine quality assessment
by use of benthic species-abundance distributions: a proposed new protocol within the
European Union Water Framework Directive. Marine Pollution Bulletin 49 (9–10), 728–
739.
DKI (Danske Kvalitet Indeks)
Borja, A., Josefson, A.B., Miles, A., Muxika, I., Olsgard, F., Phillips, G., Rodríguez, J.G., and
Rygg, B. 2007. An approach to the intercalibration of benthic ecological status
assessment in the North Atlantic ecoregion, according to the European Water Framework
Directive. Marine Pollution Bulletin, 55: 42–52.
IQI (Infaunal Quality Index)
Prior, A., Miles, A. C., Sparrow, A. J., and Price, N. 2004. Development of a classification
scheme for the marine benthic invertebrate component, Water Framework Directive.
Phase I & II- Transitional and coastal waters. Environment Agency (UK), R&D Interim
Technical Report, E1–116, E1–132: 103 p (+appendix).
Borja, A., Josefson, A.B., Miles, A., Muxika, I., and Olsgard, F., Phillips, G., Rodríguez, J.G.,
and Rygg, B. 2007. An approach to the intercalibration of benthic ecological status
assessment in the North Atlantic ecoregion, according to the European Water Framework
Directive. Marine Pollution Bulletin, 55: 42–52.
Miles, A. C., Phillips, G. R., Brooks, L. F, and Martina, L. J., in prep. The development of a
Marine Infaunal Quality Index (IQI) for UK WFD assessment. Environment Agency
(UK), R&D Technical Report.
NQI (Norwegian Quality Index)
Rygg, B. 2002. Indicator species index for assessing benthic ecological quality in marine
waters of Norway. Norwegian Institute for Water Research, Report Nº 40114: 1–32.
Rygg, B. 2006. Developing indices for quality-status classification of marine sort-bottom
fauna in Norway. Norwegian Institute for Water Research, Report Nº 5208: 1–32.
Borja, A., Josefson, A. B., Miles, A., Muxika, I., Olsgard, F., Phillips, G., Rodríguez, J. G.,
and Rygg, B. 2007. An approach to the intercalibration of benthic ecological status
assessment in the North Atlantic ecoregion, according to the European Water Framework
Directive. Marine Pollution Bulletin, 55: 42–52.
Multivariate and modelling approaches:
Several software packages can be used for multivariate and modelling approaches e.g.
PRIMER, Canoco.
Benthic Response Index
Smith, R.W., M. Bergen, S.B. Weisberg, D. Cadien, A. Dalkey, D. Montagne, J.K. Stull and
R.G. Velarde, 2001. Benthic response index for assessing infaunal communities on the
southern California mainland shelf. Ecological Applications, 11: 1073–1087.
Estuarine Trophic status
Bricker, S. B., Ferreira, J. G., and Simas, T. 2003. An integrated methodology for assessment
of estuarine trophic status. Ecological Modelling, 169: 39–60.
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Principal Response Curves (PRC)
Pardal, M. A., Cardoso, P. G., Sousa, J. P., Marques, J. C. and Raffaelli, D. 2004. Assessing
environmental quality: a novel approach. Marine Ecology Progress Series, 267: 1–8.
m-AMBI
Borja, A., Franco, J., Valencia, V., Bald, J., Muxika, I., Belzunce, M. J., and Solaun, O. 2004.
Implementation of the European Water Framework Directive from the Basque Country
(northern Spain): a methodological approach, Marine Pollution Bulletin, 48(3-4): 209–
218.
Muxika, I., Borja, Á. and Bald, J. 2007. Using historical data, expert judgement and
multivariate analysis in assessing reference conditions and benthic ecological status,
according to the European Water Framework Directive, Marine Pollution Bulletin, 55:
16–29.
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Annex 15: Di f fer e nt im pa ct s o ur ces a nd g eo gr ap hi ca l areas
for which AMBI ha s be e n a pplied , in re ce nt ye ars
Table A15.1: Different impact sources and geographical areas for which AMBI has been applied,
in recent years. Response: (+) when the AMBI responds to the pressure or impact gradient; (-)
when it does not respond; (+/-) when there are examples of both or it is not conclusive. P.c.:
personal communication.
IMPACT SOURCES
LOCATIONS (COUNTRIES)
SEAS
AUTHOR
RESPONSE
Eutrophication, sewage sludge disposal (United Kingdom)
Atlantic
A. Miles in Borja et al. (2007)
+
Oil platforms
Atlantic
Flaten et al 2007
+/-
Norway
Outfall and harbour
Brittany (France)
Atlantic
Borja et al., 2003a
+
Metal pollution
Adour (France)
Atlantic
Monperrus et al. 2005
+/-
Recovery of mudflats
Basque Country (Spain)
Atlantic
Aguirrezabalaga et al. 2004
+
Engineering works (dyke)
Basque Country (Spain)
Atlantic
Borja et al., 2000, 2003a
+
Sewerage works
Basque Country (Spain)
Atlantic
Borja et al., 2000, 2003a
+
Harbour construction
Basque Country (Spain)
Atlantic
Muxika et al., 2005
+
Submarine outfall
Basque Country (Spain)
Atlantic
Borja et al., 2000; 2003b
+
Anoxia-hypoxia, water treatment
Basque Country (Spain)
Atlantic
Borja et al., 2006
+
Harbour and river inputs
Basque Country (Spain)
Atlantic
Muxika et al., 2003
+
Various sources
Tejo estuary (Portugal)
Atlantic
M.J. Gaudencio (p.c., 2003)
+
Eutrophy
Mondego estuary (Portugal)
Atlantic
Salas et al., 2004
+
Eutrophy
Mondego estuary (Portugal)
Atlantic
Chainho et al., 2006
+
Organic and inorganic pollutants
Obidos lagoon (Portugal)
Atlantic
Carvalho et al. 2006a
+
Pond aquaculture
Ria Formosa lagoon (Portugal) Atlantic
Carvalho et al. 2006b
+
Impact gradient (outfall?)
Portugal
Chenery and Mudge (2005)
+
Atlantic
Heavy metals
Huelva (Spain)
Atlantic
Borja et al., 2003a
+
Estuarine inputs
Cádiz (Spain)
Atlantic
A. Rodríguez-Martín (p.c., 2003)
+
Various sources
(Morocco)
Atlantic
Bazairi et al. 2005
+
Various sources
Latvia
Baltic
V. Jermakovs (p.c., 2004)
+
Anoxia-hypoxia
Sweden
Baltic
Muxika et al., 2005
+
Dredging mud disposal
Sweden
Baltic
S. Smith (p.c., 2003)
+/-
Various sources in a lagoon
Smir (Morocco)
MediterraneanA. Chaouti (p.c., 2003)
+
Dredging in harbour
Ceuta (Spain)
MediterraneanMuxika et al., 2005
+
Diffuse pollution (mines, agriculture...) Almería and Murcia (Spain)
MediterraneanBorja et al., 2003a
+
Mining debris
Mar Menor (Spain)
MediterraneanMarín-Guirao et al. 2005
+/-
Recovery after aquaculture
Murcia (Spain)
MediterraneanSanz-Lázaro and Marín, 2006
+
Submarine outfall
Catalonia (Spain)
MediterraneanM.J. Cardell (p.c., 2003)
+
Marina
Catalonia (Spain)
MediterraneanS. Pinedo (p.c., 2003)
+
Various sources
Gula of Lions (France)
MediterraneanLabrune et al 2006
+/-
Wastewater discharge in a lagoon
(France)
MediterraneanG. Reimonenq (p.c., 2003)
+
Inputs to a coastal lagoon
Adriatic Sea (Italy)
MediterraneanCaselli et al., 2003
+
Inputs to a coastal lagoon
Pialassa Baiona (Italy)
MediterraneanPonti et al., 2002; Ponti & Abiatti 2004+
Various sources
Adriatic Sea (Italy)
MediterraneanForni and Occhipinti Ambroggi, 2004 +
Submarine outfall
Gulf of Trieste (Italy)
MediterraneanSolis-Weiss et al., 2004
Various sources
Adriatic Sea (Italy)
MediterraneanR. Simonini (p.c., 2004)
+
Submarine outfall
Saronikos Gulf (Greece)
MediterraneanBorja et al., 2003a
+
Aquaculture cages
3 locations (Greece)
MediterraneanMuxika et al., 2005
+
River inputs
Thames (United Kingdom)
North Sea
M. Davison (p.c., 2002)
+
Undefined
German Bight (Germany)
North Sea
Reiss and Kroncke, 2005
+
+
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IMPACT SOURCES
Industrial and urban pollution
LOCATIONS (COUNTRIES)
Seine estuary (France)
SEAS
AUTHOR
RESPONSE
North Sea
Dauvin et al., 2007
+/-
Oil-based drilling muds (oil platforms) 11 locations (United Kingdom)North Sea
Muxika et al., 2005
+
+
Ester-based drilling muds (oil platforms)North Sea (Netherlands)
North Sea
Borja et al., 2003a
Sand extraction
North Sea
Bonne et al., 2003; Muxika et al., 2007-
Belgium
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Flaten, G. R., Botnen, H., Grung, B., and Kvalheim, O. M., 2007. Quantifying disturbances in
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and temporal impact gradients on benthic communities in an estuarine area. ICES CM
2003/Session J-01, Tallinn (Estonia), 24–28 September, 2003.
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to new impact sources along European coasts. Ecological Indicators 5(1): 19–31.
Muxika, I., Borja, Á., and Bald, J. 2007. Using historical data, expert judgement and
multivariate analysis in assessing reference conditions and benthic ecological status,
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16–29.
Ponti, M., and Abbiati, M. 2004. Quality assessment of transitional waters using a benthic
biotic index: the case study of the Pialassa Baiona (northern Adriatic Sea). Aquatic
Conservation: Marine and Freshwater Ecosystems, 14: 31–41.
Ponti, M., Casselli, C., and Abbiati, M. 2002. Applicazione degli indici biotici all'analisi delle
comunità bentoniche degli ambienti lagunari costieri: la "Pialassa Baiona" (Ravenna).
Atti del XII Congresso Nazionale della Società Italiana di Ecologia, Urbino.
Reiss, H., and Kröncke, I. 2005. Seasonal variability of benthic indices: an approach to test the
applicability of different indices for ecosystem quality assessment. Marine Pollution
Bulletin, 50: 1490–1499.
Salas, F., Nieto, J. M., Borja, A. and Marques, J. C. 2004. Evaluation of the applicability of a
marine biotic index to characterise the status of estuarine ecosystems: the case of
Mondego estuary (Portugal). Ecological Indicators, 4: 215–225.
Sanz-Lázaro, C., Marín, A. 2006. Benthic recovery during open sea fish farming abatement in
Western Mediterranean, Spain. Marine Environmental Research, 62: 374–387.
Solís-Weiss, V., Aleffi, F., Bettoso, N., Rossin, P., Orel, G., Fonda Umani, S. 2004. Effects of
industrial and urban pollution on the benthic macrofauna in the Bay of Muggia (industrial
port of Trieste, Italy). The Science of the Total Environment, 328: 247–263.
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Annex 16: B e nt hos ec ol og i c al s t a t u s a s s e s s m e n t a n d
m o nit or i ng fo r t h e W at er F ram e wo rk Dir e ct iv e i n t h e Be lgi a n
coastal waters
By Wendy Bonne
Federal Public Service Health,
Food Chain Safety and Environment
Directorate General Environment
Marine Environment Service
Victor Hortaplein 40, box 10
B-1060 Brussels
Tel.: + 32 (0)2 524 95 18
Fax: + 32 (0)2 524 96 43
E-mail: Wendy.Bonne@health.fgov.be
Macrobenthos habitat typology
The habitat typology of the Belgian continental shelf is based on macrobenthic communities
and is in detailed described in Van Hoey et al. (2004). Four macrobenthic communities could
be discerned with typical species associations in between. These communities were each
characterized by different habitat specifications as briefly illustrated below.
Macrobenthic communities (habitats):
•
Abra alba community: shallow muddy sand
•
Nephtys cirrosa community: well-sorted mobile sands
•
Ophelia limacina – Glycera lapidum community: medium to coarse sand
•
Macoma balthica community: shallow sandy mud.
The macrobenthos status classification will be performed for these four communities
separately, based on community-oriented monitoring, to come to an overall macrobenthos
assessment for the Belgian coastal waters.
Assessment method
For the ecological quality assessment and the status classification of the benthos of the
Belgian coastal waters the BEQI method has been applied and will be used for the future
monitoring as well. The method (BEQI; Benthic ecosystem quality index), developed in the
Netherlands (NIOO), is based on the approach developed by Ysebaert and Herman (2004),
which aims to give an indication about ecosystem structure and functioning, and biological
relationships. As explained in van Hoey et al. (2007a) and as explained in the ECOSTAT
intercalibration report, this method differs from other methods developed by member states as
it does not evaluate the ecological status sampling station by sampling station, but rather uses
a set of indicators that take into account the different scales of variability in coastal and
transitional waters and aims at evaluating the water body (ecosystem) as a whole. Briefly, on
the level of the entire ecosystem (e.g. a water body) one can evaluate if the benthic
macrofauna fulfils the functional role one might expect given the current ecological
circumstances. At this level also integration with other quality measures is most appropriate,
and information on the water body can be summarised. On the subsequent level the
distribution of habitats (habitat completeness and complexity) can be evaluated. Finally the
biological quality of each distinguished habitat based on benthic macrofauna can be evaluated
(within-habitat level), with indicators that are sensitive to different types of stress and that can
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explain possible deviations. The BEQI-method on the third level evaluates the state of the
benthos within a habitat based on 4 parameters (sub-indicators): number of species, density,
biomass and species composition changes. These parameters reflect the normative definitions
as defined by the WFD. The parameter results strongly depend on the sampling effort
(sediment surface) that is deployed. Therefore, the reference values for the parameters were
calculated per ecotope from permutations (KRW program, version 1.0 developed by Peter
Herman in FORTRAN) executed over increased sampling surfaces. A minimum required
sampling surface is defined for reference values specification and status assessment.
The overall indicator primarily aims at providing a signal that is capable of showing
significant changes/deviations from a certain reference state.
Reference values and assessment
Level 1 of the BEQI method (macrobenthos’ functional role of consumption of primary
production)
Status of Belgian coastal macrobenthos: moderate (Van Damme et al., 2006)
Level 3 of the BEQI method (van Hoey et al., 2007b)
Too few data was available in the Belgian WFD benthos dataset to determine the reference
conditions for the different habitats, this could only be done for the Abra alba community
(minimal total sampling surface > 1 m²). The reference values for the three other communities
will have to be determined in future research on historical data or monitoring in the future.
Since for the Nephtys cirrosa community sufficient assessment data were available but not
enough reference data, an attempt of assessment has been made using the reference values for
the Zeeuwse kust of the Netherlands, which yields also the same community.
For the Abra alba community the indicator density is evaluated as bad, due to the very low
assessment density, whereas the number of species and similarity were evaluated as poor. The
overall EcoQ score and status for the Abra alba community in the coastal zone is poor.
The Nephtys cirrosa community is evaluated as moderate, due to the poor status of the
indicator similarity and moderate status for number of species. The density is evaluated as
good.
Some further important issues and difficulties to be highlighted:
The Belgian reference data for the different habitats is gathered in the period 1994 – 2000 and
comes not from a `natural, undisturbed` reference period, as required by the WFD. But this
reference dataset has the aim to give a reflection of the spatial and temporal variability within
the habitats.
Using the BEQI method, the changes in species richness, species composition and density
have been evaluated. Assessment and reference biomass data was not available and therefore
this indicator has not been evaluated for the Belgian coast.
The present assessment is not representative for the entire Belgian coast. The assessment
dataset is originating from a small sub-area of the Belgian coast (nearby the harbor of
Oostende). This site is strongly affected by the harbour of Oostende and beach restoration
works, it can thus be expected that the communities are considerably negatively influenced. In
the future, the monitoring will cover a wider spatial (entire coast) and temporal (few years)
scale, to have a more acceptable assessment for the entire Belgian coast for all the
communities.
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Monitoring within the WFD
In order to make an appropriate assessment of the macrobenthos, representative for the entire
coastal area, a surveillance monitoring will be performed in 2007–2008. Two times in a year
the four communities will be sampled. This will be repeated when operational monitoring is
considered necessary. For surveillance monitoring of those communities that are assessed to
have a good or high status a frequency will be applied of two times a year every three years.
For the monitoring stations plan three zones are distinguished in the Belgian coastal waters. In
each of these zones one station is located to sample nutrients, phytoplankton (chl a,
Phaeocystis). These three stations are each located in a separate Bird Directive protected area
and the two stations in the western and central zone are also located in a Habitat Directive
protected area. For the benthos four communities will be monitored with a specific amount of
samples per community spread over each of the three zones in order to give a spatially
representative data set of each community per zone.
Investigative monitoring will be further defined in autumn 2007.
References
Van Damme, S., Meire, P., Gommers, A., Verbeeck, L., Van Cleemput, E., Derous, S.,
Degraer, S., and Vincx, M., 2007. REFCOAST project: Typology, Reference condition
and Classification of the Belgian coastal waters (EV/40) Final Report. Scientific support
plan for a sustainable development policy (SPSD II). Part 2: Global change, Ecosystems
and Biodiversity. Belgian Science Policy, Brussels. 119 pp.
Van Hoey, G., Degraer, S., and Vincx, M., 2004. Macrobenthic community structure of softbottom sediments at the Belgian Continental Shelf. Estuarine, Coastal and Shelf Science,
59: 599–613.
Van Hoey, G., Drent, J., Yseebaert, T., and Herman, P., 2007. The Benthic Ecosystem Quality
index (BEQI), intercalibration and assessment of Dutch Coastal and Transitional Waters
for the Water Framework Directive. NIOO rapport 2007–02, 243 pp.
Van Hoey, G., Ysebaert, T., and Herman, P., 2007b. Update of the assessment of the Belgian
coastal waters with level 3 of the BEQI (Benthic ecosystem quality index)-method. 25 pp.
Ysebaert, T., and Herman, P.M.J., 2004. The assessment of the ecological status of coastal and
transitional waters based on benthic macroinvertebrates: classification and intercalibration
within the Water Framework Directive. Report No. NIOO-CEME report 2004-01.
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Annex 17: Met h ods us e d i n E ur ope , f o r t he W at er F ram e wor k
Di r e ct i ve B y A ng e l Bo r j a ( AZ TI - Te c na li a , Sp a i n )
The Water Framework Directive (WFD) establishes that the ecological status of surface water
bodies must be assessed, by comparing monitoring data with reference conditions (from
undisturbed areas) for each of the typologies.
When assessing the status of benthic communities, it must be taken into account the next
structural parameters:
•
The taxonomic composition and abundance
•
The ratio of disturbance sensitive taxa to insensitive taxa (by means of some
indices, such as AMBI, BQI, etc.)
•
The level of diversity
In order to accomplish with these requirements, several methods have been applied through
Europe. The metrics included in such methods can be seen in Annex 14.
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Annex 18: At l a nt i c i nt e r c a l ib r a t i o n
By Angel Borja (AZTI-Tecnalia, Spain)
The intercalibration was made for the coastal typology NEA-1, which is characterised by an
exposed poly- to euhaline subtidal habitat, with soft sediment. We used data from pollution
gradients and agreed intercalibration sites (in Good-High status), in order to have ecological
assessments from Bad to High status. The impacted areas represent different pressures:
sewage sludge dumping, submarine outfalls, etc., producing eutrophication, hypoxia, metal
pollution, etc.
We obtained a data set of 708 samples from different locations: Belgium (132), Germany (64),
Ireland (14), Spain (45), Denmark (72), United Kingdom (250), Norway (12), France,
Portugal and Netherlands. We tested four methods: UK (and RoI), Denmark (both
multimetric), Spain (factorial analysis: M-AMBI) and Norway (multimetric). Then, we have
added methods from France, Portugal and Netherlands. Each country used their own reference
conditions and ecological status boundaries. We made pairwise comparison, by linear
regression; then four-by-four comparison and kappa analysis to determine agreement (all the
methodologies and results can be seen in Borja et al., 2007).
In general, the correlations between the methods are high and highly significant. After
adjusting the previous boundaries for each of the ecological status, for each of the countries
(see Table 2), the final agreement was very high (kappa >0.86). The final result shows an
almost perfect agreement between the four studied methods (Table 3). Only between 3 and
12% of the sampling stations show disagreement between methods (this is when a method
classifies a sample as High or Good status and the other as Moderate, Poor or Bad (Table 3).
Table A18.2. Final boundaries agreed between the member states, for NEA-1.
Moderate/Good
Good/High
DK
0.53
0.67
NL
0.6
0.8
UK/IR
0.64
0.75
SP/FR/PT
0.53
0.77
N
0.81
0.92
Table A18.3. Final agreement, in terms of Kappa analysis and percentage of disagreement.
DENMARK
DENMARK
UK
SPAIN
NORWAY
UK
SPAIN
8.47%
5.51%
12.53%
0.91 (almost perfect)
0.93 (almost perfect) 0.86 (almost perfect)
0.91 (almost perfect) 0.96 (almost perfect) 0.87 (almost perfect)
NORWAY
7.91%
3.11%
11.72%
Monitoring in the Basque Country (North of Spain): an example
Although officially the monitoring for the WFD must start in 2006, in the case of the Basque
Country it started in 1995. We sample annually, in winter, in 18 water bodies (14 transitional,
and 4 coastal). In total we have 32 estuarine sampling stations and 19 coastal sampling
stations.
Sampling is made by Box corer (0.06 m2) or Van Veen (0.07 m2) grabs, both stainless steel.
We take three replicates for benthos and one for sediment. The penetration must be at least 5
cm (depending on sediment) to consider it as correct. Then the sediment is sieved with 1 mm
mesh size sieve. Biological samples are fixed in a buffered 4% formaldehyde solution (1 part
40 % formaldehyde solution and 9 parts sea water). For buffering we use sodium tetraborate
(= Borax) in excess. Samples are stained with Rose Bengal.
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In the laboratory, samples are sorted under a magnification lamp and stereomicroscope. After
identification and counting, biomass (dry weight) is determined at 60ºC until constant weight
(at least 24-48 h).
For sediments, grain size (φ-scale: silt/clay fraction < 63 µm, 125 µm, 250 µm, 500 µm, 1000
µm, 2000 µm) is determined by combining the Beckman-Coulter LS 13320 (laser diffraction)
with aquatic suspension processing module (resolution 0.04–2,000 µm) (for small particle
size) and sieving column (0.5 phi resolution) for higher grain size.
Organic matter is determined by weight loss on ignition (450 ºC, 24 h). Redox potential is
measured in situ, using a ORION 977800 platinum electrode, connected to a digital pHmeter/milivoltimeter CRISON 501 (resolution ± 1 mV).
References
Borja, A., Josefson, A. B., Miles, A., Muxika, I., Olsgard, F., Phillips, G., Rodríguez, J. G.,
and Rygg, B. 2007. An approach to the intercalibration of benthic ecological status
assessment in the North Atlantic ecoregion, according to the European Water Framework
Directive. Marine Pollution Bulletin, 55: 42–52.
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Annex 19: Si ev i ng c om pa ris o n
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Annex 20: NSBP C R R
Draft structure for Cooperative Research Report
1. Summary (H. Rees)
2. Introduction (H. Rees)
3. NSBP 2000 Data Management (E. Vanden Berghe)
3.1 Taxonomic problems
3.2. Sources of data
3.3 Database structure
3.4 Access to NSBP 2000 data
4. The North Sea environment
4.1 Synopsis and human influences (H. Rees)
4.2 Sediment particle size (H. Hillewaert)
4.3 Heavy metals in sediments (G. Irion)
5. Patterns and changes in the benthos (1986–2000)
5.1 Structure and characterising species of macro-zoobenthos communities in 2000 (E.
Rachor, S. Degraer, G. Duineveld , H. Reiss)
5.2 Changes in community structure (1986–2000) and causal influences (I. Kröncke, H. Reiss)
5.3 Species distributions (R. Smith, J. Eggleton)
5.4 (Role of) biotic/diversity indices (G. Van Hoey, H. Rees, H. Reiss, J. Craeymeersch)
5.5 Predictive modelling (W. Willems, S. Degraer)
5.6 Parallel studies (M. Schratzberger, G. Duineveld)
5.7 Structuring species: a case study. (G. Van Hoey)
6. Ecosystem interactions (1986 – 2000)
6.1 Links between infauna, epifauna and fish distributions (H. Reiss)
6.2 Functional diversity (M. Lavaleye)
6.3 Fishing practices (J. Craeymeersch, M. Lavaleye, G. Duineveld, M. Bergman)
6.4 Benthic community studies over relevant time-scales (GD, JC, HeR, ER, SG/HH, HR)
7. Conclusions (H. Rees)
8. Recommendations (H. Rees)
9. Acknowledgements
10. References
Annex 1 Collaborative projects relevant to the assessment of benthic communities of the
North Sea